United States Environmental Protection Agency Office of Toxic Substances Washington, D.C. 20460 EPA 560/5-85-003 Toxic Substances Methods for Assessing Exposure to Chemical Substances Volume 3 Methods for Assessing _ T ___Disposal of Chemical Substances EPA METHODS FOR 560 ASSESS ING E X POSLJRE 5-85 TO CHEMICAL 003 SUBSTANCES 3 EPA 560 5-05 003 METHODS FOR ASSESSING E X POSURE TO CHEMICAL SUBSTANCES 3 Hazardous Waste Research and Information Center Library One East Hazelwood Drive Champaign, IL 61820 217/333-8957 DtMCO EPA 560/5-85-003 July 1985 METHODS FOR ASSESSING EXPOSURE TO CHEMICAL SUBSTANCES Volume 3 Methods for Assessing Exposure from Disposal of Chemical Substances by Leslie Coleman Adkins, Stephen H. Nacht, John J. Dorla, Michael T. Christopher EPA Contract No. 68-01-6271 Project Officer Michael A. Callahan Exposure Evaluation Division Office of Toxic Substances Washington, D.C. 20460 U.S. ENVIRONMENTAL PROTECTION AGENCY OFFICE OF PESTICIDES AND TOXIC SUBSTANCES WASHINGTON, D.C. 20460 Digitized by the Internet Archive in 2018 with funding from University of Illinois Urbana-Champaign Alternates https://archive.org/details/methodsforassessOOadki DISCLAIMER This document has been reviewed and approved for publication by the Office of Toxic Substances, Office of Pesticides and Toxic Substances, U.S. Environmental Protection Agency. The use of trade names or commercial products does not constitute Agency endorsement or recommendation for use. Ill FOREWORD This document Is one of a series of volumes, developed for the U.S. Environmental Protection Agency (EPA), Office of Toxic Substances (OTS), that provides methods and Information useful for assessing exposure to chemical substances. The methods described In these volumes have been Identified by EPA-OTS as having utility In exposure assessments on existing and new chemicals In the OTS program. These methods are not necessarily the only methods used by OTS, because the state-of-the-art In exposure assessment Is changing rapidly, as Is the availability of methods and tools. There Is no single correct approach to performing an exposure assessment, and the methods In these volumes are accordingly discussed only as options to be considered, rather than as rigid procedures. Perhaps more Important than the optional methods presented In these volumes Is the general Information catalogued. These documents contain a great deal of non-chemlcal-speclf1c data which can be used for many types of exposure assessments. This Information Is presented along with the methods In Individual volumes and appendices. As a set, these volumes should be thought of as a catalog of Information useful In exposure assessment, and not as a "how-to" cookbook on the subject. The definition, background, and discussion of planning exposure assessments are discussed In the Introductory volume of the series (Volume 1). Each subsequent volume addresses only one general exposure setting. Consult Volume 1 for guidance on the proper use and Interrelations of the various volumes and on the planning and Integration of an entire assessment. The titles of the nine basic volumes are as follows: Volume 1 Methods for Assessing Exposure to Chemical Substances (EPA 560/5-85-001) Volume 2 Methods for Assessing Exposure to Chemical Substances In the Ambient Environment (EPA 560/5-85-002) Volume 3 Methods for Assessing Exposure from Disposal of Chemical Substances (EPA 560/5-85-003) Volume 4 Methods for Enumerating and Characterizing Populations Exposed to Chemical Substances (EPA 560/5-85-004) Volume 5 Methods for Assessing Exposure to Chemical Substances In Drinking Water (EPA 560/5-85-005) v Volume 6 Methods for Assessing Occupational Exposure to Chemical Substances (ERA 560/5-85-006) Volume 7 Methods for Assessing Consumer Exposure to Chemical Substances (EPA 560/5-85-007) Volume 8 Methods for Assessing Environmental Pathways of Food Contamination (EPA 560/5-85-008) Volume 9 Methods for Assessing Exposure to Chemical Substances Resulting from Transportation-Related Spills (EPA 560/5-85-009) Because exposure assessment Is a rapidly developing field, Its methods and analytical tools are quite dynamic. EPA-OTS Intends to Issue periodic supplements for Volumes 2 through 9 to describe significant Improvements and updates for the existing Information, as well as adding short monographs to the series on specific areas of Interest. The first four of these monographs are as follows: Volume 10 Methods for Estimating Uncertainties In Exposure Assessments (EPA 560/5-85-014) Volume 11 Methods for Estimating the Migration of Chemical Substances from Solid Matrices (EPA 560/5-85-015) Volume 12 Methods for Estimating the Concentration of Chemical Substances In Indoor Air (EPA 560/5-85-016) Volume 13 Methods for Estimating Retention of Liquids on Hands (EPA 560/5-85-017) Michael A. Callahan, Chief Exposure Assessment Branch Exposure Evaluation Division (TS-798) Office of Toxic Substances ACKNOWLEDGEMENTS This report was prepared by Versar Inc. of Springfield, Virginia, for the EPA Office of Toxic Substances, Exposure Evaluation Division, Exposure Assessment Branch (EAB) under EPA Contract No. 68-01-6271 (Task 11). The EPA-EAB Task Manager was Stephen Nacht, the EPA Program Manager was Michael Callahan; their support and guidance Is gratefully acknowedged. Acknowledgement Is also given to Elizabeth Bryan of EPA-EED, who also took part In this task. A number of Versar personnel have contributed to this task over the three-year period of performance as shown below: Program Management Gayaneh Contos Task Management Leslie Coleman Akdlns Technical Support John Dorla Michael Christopher Thompson Chambers J. Randall Freed Douglas Dixon Editing Juliet Crumrlne Secretarial/Clerical Shirley Harrison Lucy Gentry Donna Barnard Patience Miller TABLE OF CONTENTS Page FOREWORD . v ACKNOWLEDGEMENTS . vll TABLE OF CONTENTS . lx LIST OF TABLES . xl 1 LIST OF FIGURES . xv LIST OF APPENDICES . xvl 1. INTRODUCTION . 1 1.1 Purpose and Scope . 1 1.2 Limitations . 2 1.3 Overview - Potential for Exposure to Chemical Substances from Waste Disposal . 3 2. GENERAL METHODOLOGICAL APPROACH . 6 2.1 Integration with Other Exposure Scenarios . 7 2.2 Framework for Estimating Releases . 7 2.3 General Decision Trees for Stages 1 through V . 10 2.3.1 Stage I Decision Tree - Estimating Releases to Disposal . 11 2.3.2 Stage II Decision Tree - Characterizing Waste Stream Releases and Concentrations . 13 2.3.3 Stage III Decision Tree - Allocating Waste Streams to Disposal Practices . 14 (1) Incinerator residues . 19 (a) Background Information . 19 (b) Stage III decision tree . 23 (2) POTW sludge . 25 (a) Background Information . 25 (b) Stage III decision tree . 27 (3) Wastewater . 29 (a) Background Information . 30 (b) Stage III decision tree . 31 (4) Hazardous Waste . 35 (a) Background Information . 35 (b) Stage III decision tree . 38 TABLE OF CONTENTS (continued) Page (5) Nonhazardous Industrial solid waste . 41 (a) Background Information . 41 (b) Stage III decision tree . 45 (6) Municipal Solid Waste (MSW) . 46 (a) Background Information . 46 (b) Stage III decision tree . 49 2.3.4 Stage IV Decision Tree - Allocating Waste Streams to Individual Disposal Sites . 50 2.3.5 Stage V Decision Tree - Estimating Environmental Releases from Disposal Sites . 53 3. LANDFILLS . 56 3.1 Background Information . 56 3.1.1 Landfill Types and Operation . 56 3.1.2 Environmental Releases from Landfills . 57 3.1.3 Predicting Environmental Releases . 60 3.1.4 Model Input Data . 62 3.1.5 Additional Considerations for Modeling Chemical Releases from Landfills . 74 3.1.6 Estimating Emissions from Broad Geographical Regions . 82 3.1.7 Monitoring . 82 3.2 Allocating Waste Streams to Landfill Sites - Stage IV Decision Tree . 83 3.2.1 Municipal Landfills . 83 3.2.2 Industrial Nonhazardous Landfills . 84 3.2.3 Hazardous Waste Landfills . 85 3.3 Estimating Environmental Releases from Landfills - Stage V Decision Tree . 86 3.3.1 Municipal Landfills . 87 3.3.2 Industrial Landfills . 89 4. LAND TREATMENT . 91 4.1 Background Information . 91 4.1.1 Types of Waste Treated . 92 4.1.2 Environmental Impacts and Environmental Releases .. 95 4.1.3 Location of Sites . 97 4.1.4 Estimating Environmental Releases . 98 4.1.5 Model Input Data . 100 4.1.6 Monitoring . 104 4.2 Allocating Waste Streams to Land Treatment Sites - Stage IV Decision Tree . 104 4.3 Estimating Environmental Releases from Land Treatment - Stage V Decision Tree . 106 x TABLE OF CONTENTS (continued) Page 5. SURFACE IMPOUNDMENTS . 110 5.1 Background Information . 110 5.1.1 Types of Impoundments . Ill 5.1.2 Environmental Releases from Surface Impoundments .. 115 5.2 Allocating Waste Streams to Surface Impoundments - Stage IV Decision Tree . 118 5.3 Estimating Environmental Releases from Surface Impoundments - Stage V Decision Tree . 127 6. PUBLICLY OWNED TREATMENT WORKS (POTWs) . 134 6.1 Background Information . 134 6.1.1 General . 134 6.1.2 Chemical Substances In POTW Effluent and Sludge ... 136 6.1.3 Predicting Releases of Chemical Substances from POTWs . 136 6.2 Allocating Wastewater to Individual POTWs - Stage IV Decision Tree . 140 6.3 Estimating Releases from POTWs - Stage V Decision Tree ... 142 7. INCINERATION . 145 7.1 Background Information . 145 7.1.1 General . 145 7.1.2 Information Resources . 147 7.1.3 Emissions and Products of Incineration . 149 7.1.4 Estimating Emissions from Incineration . 153 7.2 Allocating Waste Streams to Individual Incinerators - Stage IV Decision Tree . 154 7.3 Estimating Emissions from Incineration - Stage V Decision Tree . 157 8. DEEP-WELL INJECTION . 161 8.1 Background Information . 161 8.1.1 General . 161 8.1.2 Information Resources Useful In Assessing the Potential for Exposure from Injection Wells . 166 8.1.3 Modeling Releases to Groundwater . 166 8.2 Allocating Waste Streams to Individual Injection Wells - Stage IV Decision Tree . 167 8.3 Estimating Releases from Injection Wells - Stage V Decision Tree . 169 REFERENCES . 172 xi LIST OF TABLES Page Table 1. Overview of Six Waste Treatment/01 sposal Methods. 4 Table 2. Characteristics of Municipal Incinerator Residue from Two Studies. 20 Table 3. Average Analysis of Water-Soluble Portion of Residue from Selected Municipal Incinerators. 21 Table 4. Chemical Analysis of Fly Ash Samples from a Municipal Incinerator. 22 Table 5. Average Characteristics of Sewage Sludge. 26 Table 6. Current Nationwide Disposal Practices for POTW Sludge. 28 Table 7. Populations Served by Wastewater Treatment Types. 32 Table 8. Hazardous Waste: Possible Disposal Methods. 37 Table 9. OSW Industrial Hazardous Waste Assessment Reports. 39 Table 10. Industrial Solid Waste Production. 42 Table 11. Sludge Generation by Manufacturing Industries. 43 Table 12. Nonhazardous Industrial Solid Waste: Disposal Methods. 44 Table 13. Composition and Analysis of an Average Municipal Refuse_ 47 Table 14. Municipal Solid Waste: Disposal Practices. 48 Table 15. Characteristics of MSW Leachates Reported In Five Studies. 59 Table 16. Precompiled Soil Parameters, SESOIL Data File. 64 Table 17. Selected Data from the 1983 Waste Age Survey. 66 Table 18. Landfill Size and Capacity Estimates. 68 Table 19. Recommended Design Criteria for Disposal of Municipal Sludge In Landfills. 72 xi i LIST OF TABLES (continued) Page Table 20. Off-Site Hazardous Landfill Area Utilized Annually. 75 Table 21. Commercial Off-Site Hazardous Waste Disposal Facilities Offering Landfilling Services In 1980 by EPA Region. 76 Table 22. Industrial On-Site Landfills by State. 77 Table 23. Estimated Number of Industrial Landfills by Size Category. 78 Table 24. Industrial On-Site Landfill Acreage Used Annually. 80 Table 25. Municipal Landfill Acreage Used Annually. 81 Table 26. Landspreading Activity, Dry Weight. 93 Table 27. Commercial Off-Site Hazardous Waste Disposal Facilities Offering Land Treatment/Solar Evaporation Services In 1980 by EPA Region. 96 Table 28. Annual Land Treatment Application Rates. 103 Table 29. Summary Statistics for Active Surface Impoundment Sites Located In the SIA. 112 Table 30. Liner Data, Municipal Impoundment Sites. 114 Table 31. Distribution of Industrial Impoundment Sites by SIC Code.. 116 Table 32. Liner Data Industrial Impoundment Sites. 117 Table 33. Inventory of Pits, Ponds, and Lagoons from 1981 Waste Age Survey. 121 Table 34. Sludge Generation Factors In Wastewater Treatment. 138 Table 35. Solids Content In Sludges In Relation to Treatment. 139 Table 36. Commercial Off-Site Hazardous Waste Disposal Fac111 111es Offering Incineration Services In 1980. 148 Table 37. Emission Factors from Sludge Incineration. 150 Table 38. Summary of Total Organic Chlorine (T0CI) Inputs and Emissions at the Chicago Northwest Incinerator. 151 xi i i LIST OF TABLES (continued) Page Table 39. Organic Compounds Quantitated In the Emission Media for the Chicago Northwest Incinerator. 152 Table 40. Classification and Types of Injection Wells. 163 Table 41. Standard Industrial Classification of Injection Wells.... 164 Table 42. Commercial Off-Site Hazardous Waste Disposal Facilities Offering Deep-Well Injection Services In 1980 by EPA Region. 165 xiv LIST OF FIGURES Page Figure 1. Important Disposal Patterns for Major Waste Types. 5 Figure 2. Overview of Five-Stage Framework for Estimating Environmental Releases from Disposal. 8 Figure 3. Stage I and II Flow Chart. 12 Figure 4. Summary of Stage III: Allocating Waste Streams to Disposal Methods. 15 Figure 5. Key for Determining Stage III Starting Point. 17 Figure 6. Summary of Stage IV: Allocation of Waste Streams to Individual Disposal Sites. 51 Figure 7. Summary of Stage V: Estimating Environmental Releases from Disposal Sites. 54 xv LIST OF APPENDICES Page No. GUIDE TO APPENDICES . 183 APPENDIX A INFORMATION RESOURCE MATRIX: USEFUL MODELS AND DATA BASES . 189 APPENDIX B SUMMARY OF INFORMATION COLLECTED FROM STATE SOLID WASTE AGENCIES . 195 Exhibit B-l. Selected Reports on Waste Generation and Disposal Prepared by State Solid Waste Agencies . 197 Exhibit B-2. State Inventories of Disposal Facilities . 198 APPENDIX C INFORMATION ON WASTE DISPOSAL PRACTICES OF SELECTED INDUSTRIES . 199 Table C-l. Summary of Hazardous Waste Generation and Disposal In 1980 for Selected Chemical Manufacturing and Petroleum Refining Industrial Segments by EPA Region . 201 Table C-2. Hazardous Waste Constituents - Petroleum Rerefining (SIC 2992). 202 Table C-3. Disposal Practices - Petroleum Rerefining . 203 Table C-4. Hazardous Waste Constituents - Petroleum Refining . 204 Table C-5. Disposal Practices - Petroleum Refining . 205 Table C-6. Disposal Practices - Organic Chemicals (SIC 2861, 2865, 2869, except 28694) . 206 Table C-7. Hazardous Waste Treatment/Dlsposal Methods - Selected Organic Chemical Plants . 207 Table C-8. Hazardous Waste Treatment/Dlsposal Methods at Selected Organic Chemical Plant Sites . 208 APPENDIX D INFORMATION IN SUPPORT OF STAGE III . 215 Exhibit D-l. The Hazardous Waste Data Management System (HWDMS) . 217 Table D-l. POTWs: Treatment Populations - Present and Projected, Resident and Nonresident . 219 Table D-2. POTWs: Average Domestic Flows by State - Present, Projected, and Percent Change . 222 xvi LIST OF APPENDICES (continued) Page No. Table D-3. State Solid Waste Agencies U.S. Environmental Protection Agency Office of Solid Waste . 225 Table D-4. Hazardous Waste Treatment, Storage, and Disposal Process Codes Used In HWDMS . 232 Table D-5. Information on Hazardous Wastes Listed by RCRA In the Federal Register on May 19, 1980 . 234 Table D-6. Applicability of Available Incineration Processes to Incineration of Hazardous Waste by Type . 243 Table D-7. Compilation of HWDMS Data . 244 Table D-8. Industries Subject to Effluent Limitation Guide¬ lines and Pretreatment Standards . 245 APPENDIX E AUXILIARY INFORMATION ON LANDFILLS AND LAND TREATMENT . 247 Table E-l. Estimation of U.S. Population In Environmentally Sensitive Areas . 249 Table E-2. Selected Data on Landfills from 1981 Waste Age Survey . 255 Table E-3. Input Data for SESOIL . 259 Table E-4. Geographic Distribution, by Region and State, of Hazardous Waste Land Treatment Sites In the U.S. .. 262 Table E-5. Industrial Classification and Location of Hazardous Waste Land Treatment Facilities . 264 Figure E-l. Areal Distribution of Land Treatment Facilities .. 270 Figure E-2. Size Distribution of Hazardous Waste Land Treatment Facilities . 271 APPENDIX F AUXILIARY INFORMATION ON GROUNDWATER . 273 Table F-l. Computerized Groundwater Data Bases . 275 Table F-2. Listing of State Geologists - 1983 . 276 Figure F-l. Concentration of Wetlands In the U.S. 284 APPENDIX G AUXILIARY INFORMATION ON SURFACE IMPOUNDMENTS . 285 Table G-l. Relation Between Surface Impoundment Assessment (SIA) Rating and Raw Data . 287 Table G-2. Relation Between SIA Earth Material Categories and the Unified Soil Classification System . 289 xvi i LIST OF APPENDICES (continued) Page No. APPENDIX H AUXILIARY INFORMATION ON POTWs . 291 Exhibit H-l. Needs Survey . 293 Exhibit H-2. Industrial Facility Discharge File (IFD) . 294 Table H-l. Occurrence of Priority Pollutants In POTW Influents: Part 1 - Plants 1 to 40 . 295 Table H-l. Occurrence of Priority Pollutants In POTW Influents: Part 2 - Supplemental Plants 51 to 60 . 298 Table H-2. Summary of Selected Influent Pollutant Concentrations for POTWs 1 through 40 . 300 Table H-3. Occurrence of Priority Pollutants In POTW Effluents: Part 1 - Plants 1 to 40 . 301 Table H-3. Occurrence of Priority Pollutants In POTW Effluents: Part 2 - Supplemental Plants 51 to 60 . 303 Table H-4. Occurrence of Priority Pollutants In POTW Raw Sludges: Part 1 - Plants 1 to 40 . 305 Table H-4. Occurrence of Priority Pollutants In POTW Raw Sludges: Part 2 - Supplemental Plants 51 to 60 ... 307 Table H-5. Summary of Minimum Percent Removals Achieved by Secondary Treatment . 309 Table H-6. Median Percent Removals of Selected Pollutants Through POTW Treatment Process . 311 Table H-7. Summary of Priority Pollutant Occurrence In Sludge When Not Detected In Influent . 312 Table H-8. Summary of Treatment and Sludge Handling Processes - Numbers of Plants and Associated Flow - United States Totals . 313 APPENDIX I AUXILIARY INFORMATION ON INCINERATION . 317 Figure 1-1. Geographic Distribution of Sewage Sludge Incinerators Proposed, Under Construction, or In Operation, 1978 319 Table 1-1. 1981 Inventory of Resource Installations from Waste Age Survey . 320 Table 1-2. Inventory of Small Municipal Incinerators . 335 Table 1-3. Inventory of Large Municipal Incinerators In Operation In 1980 . 336 Table 1-4. Manufacturing Segment of the National Industrial Incinerator Population by Use Category . 337 Table 1-5. Hazardous Waste Incinerator Vendor Data for the United States . 338 Table 1-6. Summary of Emission Test Data from Municipal Incinerators . 344 Table 1-7. Summary of Emission Test Data from Liquid Waste Incinerators . 345 Table 1-8. Hazardous Wastes Rated as Good, Potential, or Poor Candidates for Incineration by Appropriate Technologies . 346 xvi i i LIST OF APPENDICES (continued) Page No. Table 1-9. Trial Burn Summaries . 362 Table I-10. Potential Air Pollutants from Hazardous Waste Incineration . 368 Table 1-11. Part 1: Heat of Combustion of Organic Hazardous Constituents from Appendix VIII, 40 CFR Part 261 . 369 Table 1-11. Part 2: Ranking of Inclnerabl11ty of Organic Hazardous Constituents from Appendix VIII, 40 CFR Part 261, on the Basis of Heat of Combustion . 374 Table 1-12. Hazardous Waste Incineration Processes and Their Typical Operating Ranges . 379 Table 1-13. Polycyclic Aromatic Hydrocarbon (PAH) Emissions from Municipal Solid Waste Incinerators In Micrograms per Kilogram of Refuse Charged . 380 Table 1-14. Polycyclic Aromatic Hydrocarbon (PAH) Levels In Air Emissions, Solid Waste Residues, and Scrubber Water Discharge from a Municipal Solid Waste Incinerator . 381 APPENDIX J AUXILIARY INFORMATION ON DEEP-WELL INJECTION . 383 Table J-l. Compounds that have been Disposed of by Deep-well Injection . 385 Table J-2. Modified Thels Equation . 389 Table J-3. Information on the Survey Waste Injection Program (SWIP) . 390 APPENDIX K USEFUL CONVERSION FACTORS . 393 Table K-l. Useful Conversion Factors . 395 XT X INTRODUCTION 1 . This report presents methods and supporting Information for estimating environmental releases from the disposal of wastes. Companion volumes provide procedures for assessing the following other exposure scenarios: the ambient environment (Volume 2), drinking water (Volume 5), the occupational environment (Volume 6), consumer products (Volume 7), food (Volume 8), and transportation-related spills (Volume 9). An Introduction to the entire methods development series Is In Volume 1 and recommended methods for enumerating and characterizing populations are presented In Volume 4. The purpose, scope, and limitations of this volume are discussed below, followed by an overview of the problem of exposures to chemical substances from disposal. The methodological framework Is presented In Section 2, and applications of the methods to selected waste disposal practices are presented In Sections 3 through 8. 1.1 Purpose and Scope This document provides procedures for estimating environmental releases from waste disposal activities used In exposure assessments performed by the U.S. Environmental Protection Agency (EPA) Office of Toxic Substances (OTS) under the mandate of the Toxic Substances Control Act (TSCA). The present volume must be used together with Volumes 2, 5, and 7, which deal with the ambient, drinking water, and consumer exposure scenarios, respectively. Volumes 2 and 7 are used to develop Information on quantities and characteristics of the subject waste. Starting with this Information, the present volume guides the assessor through the assumptions, calculations, and estimations that are required to characterize and quantify releases to air, land, and water. The assessor must then return to Volumes 2 and 5 to relate these releases to ultimate exposure, thereby completing the assessment. See Volume 1 for a discussion of the nature and purpose of exposure assessments In general as well as for a more detailed explanation of the Interrelations and Integration of the various volumes. A separate volume was created for the disposal setting because of the need to develop a detailed Information base for what Is assumed to be a major source of environmental releases of toxic substances. This volume fills a need In the discipline of exposure assessment because there exists no comprehensive Information source covering the range of topics and data sources that must be considered In estimating chemical releases from waste disposal. 1 Methods are developed to the greatest extent possible for six waste treatment/dlsposal practices that have a great potential for environmental contamination either because they handle relatively large quantities of waste or because they have been known to release significant quantities of toxic substances to the environment. These practices are: landfilling, land treatment, surface Impoundment, municipal wastewater treatment. Incineration, and deep-well Injection. Methods for estimating environmental releases resulting from storage of wastes prior to disposal are not provided except In the case of storage In surface Impoundments. Similarly, with the exception of wastewater treatment and Incineration, waste handling methods that are purely treatment (as opposed to ultimate disposal) techniques were not Included In the volume. (Treatment consists of any process designed to change the physical, chemical, or biological character or composition of a waste for the purpose of making It safer for transport, amenable to recovery or storage, or reduced In volume. Examples Include neutralizing a strong acid, degrading a chemical compound, or sterilizing Infectious waste.) It should be emphasized that the scope of this report Is limited to methods leading to estimation of environmental releases from disposal sites and that the companion volumes must be consulted In order to complete the exposure assessment. See Volume 1 of this series for guidance on this. 1.2 Limitations This methodology represents the synthesis of a large body of Information from a variety of sources. The five-stage framework approach should be applicable to any waste treatment or disposal method. The Information base represented In both the site-specific and the generic data presented In this report Is likely to expand In the next few years. For the present, however, there are significant data and model gaps that can be filled only by making assumptions and/or using predictive techniques that are largely untested. Some of these assumptions can be evaluated with respect to their uncertainty using a sensitivity analysis, but other data and model gaps cannot presently be compensated for. For Instance, the effect of other constituents In a waste matrix on the chemical of Interest Is very chemical-specific and little understood. A related Issue Is the problem of determining which new, potentially toxic compounds may be formed during treatment or disposal of the subject chemical and how fast they will be released from the waste matrix. This can be answered only through further research. In the meantime, the user will have to decide whether collecting detailed data In several stages of the methodology Is worthwhile If other stages cannot be accurately quantified. 2 1.3 Overview - Potential for Exposure to Chemical Substances from Waste Disposal The number of steps In the waste handling process varies considerably, depending on the nature and source of the waste and available waste handling methods. The disposal process for a consumer product discarded In residential waste that Is taken to a landfill Is quite simple. However, the fate of the chemical constituents In that consumer product may be complex, and some of a given chemical may end up In the air, some on land, some In groundwater, and some In surface waters. The picture Is even more complex for the chemical constituents of a consumer product washed down a drain and routed to a sewage treatment plant. 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XD o E TD 2 2 2 a 3 3 i_ CO Q- CL < < < < < U TJ © CD XI — 4 INDUSTRY GO 5 Figure 1. Important Disposal Patterns for Major Waste Types 2 . GENERAL METHODOLOGICAL APPROACH The methods development series Is designed to fulfill the wide-ranging needs associated with assessing exposure from chemical substances. Although tailored specifically for use In exposure assessments required under TSCA, the approach should be applicable to all types of exposure assessments that Include the disposal scenario. In order to provide a useful tool for current and future studies, the method has to be: • Comprehensive, In that all possible waste types and disposal methods can be evaluated using a consistent procedure. • Flexible, so that It can be used for all kinds of assessments, ranging from detailed site-specific studies to large-scale nationwide assessments, and can be easily modified as new sources of Information become available. • Reliant on readily available sources of data. • Amenable to the Input of site- and chemical-specific data, as well as to generic data, algorithms, and models. • Applicable to assessing exposure from waste-handling practices that Include one or more steps (e.g., treatment prior to disposal). Based on these criteria, a five-stage framework was developed for the present volume which leads the user from source Information compiled from a materials balance and the results of preliminary ambient and consumer exposure assessments to the final estimation of environmental releases from disposal sites. For each stage In the framework, a general procedure was developed for estimating the output of that stage. These procedures will be referred to as "decision trees." These general decision trees were then tailored to those waste categories and disposal methods considered to be the most significant sources of exposure to chemical substances. Section 2.1 provides an overview of how this volume fits Into a complete exposure assessment. The five-stage framework Is presented In Section 2.2, and the general decision trees applicable to each of the five stages are presented In Section 2.3. Finally, the applications of this approach to the six disposal/treatment categories selected for Investigation (landfills, land treatment, surface Impoundments, sewage treatment plants, Incinerators, and Injection wells) are developed In Sections 3 through 8. 6 The procedures suggested In this volume are based on a review of available literature and data bases, and contacts with EPA and state solid waste agency personnel. A resource matrix summarizing Important Information sources Is given In Appendix A. Appendices B through J contain summaries or sample data from Information resources that may be useful In Implementing the suggested procedures. A list of useful conversion factors Is presented as Appendix K. 2.1 Integration with Other Exposure Scenarios It cannot be overemphasized that this volume does not constitute a self-contained exposure assessment method, but falls entirely within the scope of the source analysis required for an ambient (or drinking water) exposure assessment. This Is true even when only disposal-related exposure Is being assessed. The Input to the disposal analysis Is quantitative and qualitative Information on the subject waste that must be provided, at least In part, by procedures discussed In the companion volumes on the ambient and consumer settings (Volumes 2 and 7, respectively). The ultimate output of the disposal analysis consists of quantitative estimates of releases, substance concentrations, and release characteristics for the relevant disposal methods. This Information does not by Itself constitute the desired output of a complete exposure assessment; It Is mere raw data which must be Input to an ambient (and/or drinking water) analysis. It Is these latter analyses which will determine the subject chemical's fate and the ultimate environmental concentrations to which receptors may be exposed. A separate population analysis must also be conducted (see Volume 4). Consult the Introductory volume to this series (Volume 1) for a more detailed discussion of how the Individual volumes are used together to perform an Integrated assessment. This volume Is designed to be useful for assessments of any scope and depth, as explained In the following subsection. The desired scope and depth of the assessment should be determined before the actual analysis Is begun. However, the original scope and depth may have to be modified In the course of the assessment In response to unexpected data limitations or other factors. See Volume 1 of this series for guidance on these and similar planning Issues. 2.2 Framework for Estimating Releases A five-stage framework for estimating chemical releases to air, surface waters, groundwater, and land from disposal Is presented as Figure 2. The framework forms the foundation of this method by outlining the major steps that must be taken to estimate releases from disposal sites regardless of the disposal practice. The Input to the 7 8 FIGURE 2 OVERVIEW OF FIVE STAGE FRAMEWORK FOR ESTIMATING ENVIRONMENTAL RELEASES FROM DISPOSAL framework Is Information on the waste that will be partially provided by the ambient and consumer exposure scenarios and a materials balance. Two types of output result from the Initial use of the framework. The first consists (at least Ideally) of quantitative estimates of releases, chemical concentrations, and release characteristics for ultimate disposal methods, as discussed previously. The other output consists of quantitative Information on secondary treatment residues that result from waste treatment practices. The latter may serve as Input for another Iteration of the framework to quantify releases from ultimate disposal of the residues. Total estimated releases from all treatment and disposal of the subject waste are used as Input to an ambient and/or drinking water analysis to complete the assessment (see Volume 1). The framework Is organized as follows: Stage I Involves determining the total mass of the chemical that Is disposed of from a given source. The source may be one or more Industrial plants, commercial users, or consumer users. Stage II entails estimating the mass and concentration of the chemical In each waste stream, along with the characteristics of the waste matrix In which It Is Incorporated (e.g., municipal solid waste, sludge). One source may produce several waste streams containing a given chemical; for example, a consumer may flush a cleaning agent down a drain and later discard Its container In the household garbage. Stage III estimates the proportion of each subject waste stream that Is disposed of by each available disposal method. If the source of the waste stream Is a single manufacturing plant, then 100 percent of the waste stream may be disposed of by one method. If more than one source contributes to the waste stream, or If the waste stream results from consumer use, then more than one disposal method will probably be Involved. Stage IV Is the quantitative estimation of how the subset of waste handled by each disposal method Is distributed among Individual disposal sites. For example, Stage III may estimate that 80 percent of a given waste stream Is landfilled; Stage IV then estimates how much of the landfilled portion of the waste stream Is taken to each specific landfill location. This stage can be omitted In assessments that do not require site-specific data, as determined before beginning the assessment (see Volume 1). The user should read the applicable decision tree for Stage IV In any case, since It may provide options or alternatives depending on the degree of site-specificity desired. Stage V estimates environmental releases of the disposal sites enumerated In Stage IV. For the subject chemical from assessments that are not 9 site-specific, releases can be estimated for a statistically representative sample of disposal sites or from one hypothetical site that Is designed to be representative of all sites. The Stage V decision trees are designed to be useful for any of these alternatives; a general discussion of the different approaches Is presented briefly In Volume 1 of this series. The user should note that the framework need not be followed In sequence from Stage I to Stage V for all wastes. For example, If Information has already been compiled on the quantity of waste handled by each disposal method for a particular substance (the equivalent to the output of Stage III), the assessor can start at Stage IV of the procedure. Wastes that are products of waste treatment (such as Incinerator residues) are characterized In Stage V of the treatment analysis. These characteristics (mass of chemical, concentration of chemical, and mass or volume of waste matrix or treatment residue) are used as Input to Stage III In order to complete that estimation of environmental releases. In the case of wastewater, a number of very different treatment/disposal methods may be used sequentially on-site (e.g., surface Impoundments, tanks, land treatment). Thus, the framework from Stage III through Stage V may be repeated several times to estimate total environmental releases from sewage treatment plants (POTWs). The types of data required by the framework depend on the particular stage and the waste type and disposal method of Interest. Data types Include: (1) site-specific or chemical-specific data from a data base, federal or state agency files, or a document; (2) general data compiled from data bases or documents; (3) algorithms; and (4) models. In any given step of a stage, the user may be limited to one of the above because of availability, or may be presented with a choice based on the scope, depth, and approach of the assessment (see Volume 1). 2.3 General Decision Trees for Stages I Through V This section contains the general decision trees that were developed for each of the five stages of the disposal framework. They outline the factors that should be routinely considered when this method Is used. They are the basis for the detailed decision trees presented In Sections 3 through 8, which are Individually tailored to each disposal practice. Future expansions of this method to Include waste disposal/treatment practices not examined In this report will be facilitated If the general decision trees are used as guidance. Not every step In the decision trees will apply to all wastes or disposal practices. The wide variety of method applications and Information sources make a single "cook book" approach to estimating environmental 10 releases from disposal Impractical. Successful use of the methods recommended In this report, therefore, depends on an understanding of the following factors: (1) the relationship of each step to the desired output; (2) the relationship between the various steps and stages; and (3) an acquaintance with useful Information resources. Graphical summaries of the major steps and key outputs are provided for each stage In the five-stage framework to orient the Inexperienced user. These figures, as well as Figure 2 presented previously, should be consulted as often as necessary to maintain perspective when applying the procedures outlined In this report to practical exposure assessment problems. The data required as Input for each stage generally consist of the output of the previous stage, with the exception of residual wastes that are produced by waste treatment (as opposed to disposal) methods. In that case, the output of Stage V for the treatment process will become the Input of Stage III of the disposal process. The user should keep track of the quantitative uncertainty associated with each step or estimate. Because of the limited nature of many of the data, the estimate of uncertainty will be coarse and will be expressed as an order of magnitude or a range of observed values. Obviously, the user should perform a statistically based analysis of uncertainty If the data warrant such an approach. Stages I and II of the framework are based entirely on outputs from the ambient and consumer exposure analyses (Volumes 2 and 7) and a materials balance and are estimated only once (and In direct sequence) for a given source of waste. Stage III Is performed once for each waste stream enumerated In Stage II. Stages IV and V are conducted once (and In direct sequence) for each disposal practice applicable to the waste stream. (See Figure 2 .) 2.3.1 Stage I Decision Tree - Estimating Releases to Disposal A flow chart summarizing the steps In Stages I and II Is presented In Figure 3. The Input for this stage Is derived from a materials balance and the results of preliminary ambient and consumer exposure assessments. Methods for analyzing the ambient and consumer settings are presented In Volumes 2 and 7 of this series; a materials balance will generally have been prepared prior to, or as part of, these analyses. The typical materials balance may not provide sufficient resolution for Stage I of a very detailed disposal analysis; In this case, engineering expertise may be required to help predict waste characteristics and quantities. 11 STAGE I-SECT. 2.3.1 12 Figure 3. Stage I and II Flow Chart Step 1 . List all likely sources of waste containing the subject chemical, Including: a. Industries Involved In primary and secondary production. b. Commercial users. c. Consumer users. Data for 1.a may be derived from a materials balance and the results of a preliminary ambient exposure assessment (Volume 2). For l.b and l.c, first enumerate the end products containing the chemical, and then determine the potential for use In the commerclal/consumer sector. Relevant Information may be obtained from the results of a preliminary consumer exposure assessment (Volume 7), and, In the case of l.b, a materials balance. Step 2 . For each source/use listed In Step 1, estimate the amount of the subject chemical disposed of annually, again based on a materials balance and Information collected for the ambient and consumer exposure analyses. The output of Stage I should be a list of sources/uses of waste containing the subject chemical and estimates of the quantities of the chemical ultimately disposed of from each source/use. 2.3.2 Stage II Decision Tree - Characterizing Waste Stream Releases and Concentrations A flow chart summarizing the steps In Stage II was presented In Figure 3. The goal of this stage Is to characterize the Individual waste streams that are included In the total waste quantities estimated In Stage I. This must be done both quantitatively and qualitatively. The Input for this stage will be derived from the same sources as the Stage I Information; In fact, It may already have been compiled In order to estimate the Stage I output. As In Stage I, engineering expertise may be required. Step 1 . For each source/use of the subject chemical listed In Stage I, determine whether the resulting waste Is likely to be separated Into different waste streams prior to disposal. If different waste streams are combined prior to disposal, only the combined waste stream need be considered. For each combined waste stream, estimate the total annual quantity of the chemical disposed of (kkg/year) and the total volume or mass of the waste stream containing the chemical. In addition, list other known physical/chemical characteristics of the waste matrix that are relevant to disposal, Including other chemicals and minerals present (and their concentrations) and the physical state (e.g., liquid, solid, sludge). This will provide a profile of each waste stream that will be useful for Stage III determination of likely disposal methods and Stage V estimates of releases. 13 Consider the following: • For Industrial wastes, this determination will be based largely on a materials balance and engineering judgment. • For the commercial use sector, the distribution of discarded consumer products among various waste streams will depend largely on the waste handling practices In use, which are limited. For many commercial establishments, the wastes will be aggregated Into one of two waste streams: sewage (l.e., wastewater) and solid waste. In addition, solid waste may sometimes be separated Into more than one category based on size and nature of wastes. In the absence of specific Information, however, assume that commercial products are discarded In the same waste streams as are consumer use products. • For the consumer use sector. It can generally be assumed that waste will be discarded In either of two waste streams: wastewater or municipal solid waste. Their relative amounts may be determined from Information on the use of the applicable consumer product(s) compiled for the consumer exposure scenario (Volume 7). Quantitative Information on the lifetime of consumer products and how much of the chemical substance Is contained In products at the time of disposal may have been compiled for the consumer portion of the exposure assessment. Otherwise, Consumer Product Safety Commission (CPSC) publications such as Lahr and Gordon (1980) may be helpful. The output of Stage II should Include the following for each waste stream from each source of waste containing the subject chemical: • Name or description of waste stream • Annual loading of subject chemical (mass/year) • Volume of mass of waste matrix containing subject chemical (quantity/year) • Destination of waste stream (l.e., land or sewers) • Relevant chemical/physical properties of waste stream • Information on the source of waste stream, Including location and SIC Code, If relevant (from Stage I). 2.3.3 Stage III Decision Tree - Allocating Waste Streams to Disposal Practices The steps In this decision tree are summarized In Figure 4. This stage In the disposal framework determines the disposal/treatment practices likely to be employed for a given waste stream and estimates the amounts of waste disposed of by each of the Identified practices. 14 15 FIGURE 4. SUMMARY OF STAGE III: ALLOCATING WASTE STREAMS TO DISPOSAL METHODS The Input to Stage III for a given waste stream Is Information on the source, waste generation rate (volume or mass per time), chemical concentration, and physical state of the waste stream. Using this Information and the decision trees provided In this section, the user estimates the quantity of subject waste destined for each likely disposal practice. The output of Stage III serves both as a starting point and as a check point for the site-specific Stage IV estimates. One feature of this approach Is that It allows various levels of refinement, depending on the needs and resources of a given exposure assessment. An example Is the method for arriving at Stage III estimates. The preliminary Stage III estimates can be based on readily available precompiled Information on regional or national disposal practices. For exposure assessments that treat the disposal scenario superficially, these "gross" estimates may be the end point of the Investigation. In cases where a more refined estimate Is desirable, however, the user can take advantage of available site-specific data suggested In the Stage IV methods, and use this Information to re-evaluate the original Stage III estimates. Thus, the Stage III and Stage IV estimates will often he Iterative and should be compared carefully In order to produce compatible estimates of waste quantities for all general practices and specific disposal sites. The procedure for determining the disposal practice likely to handle a given waste stream Is organized by waste category. Six general waste categories were selected to be addressed In this report. These are: Incinerator residues, POTW sludge, wastewater, hazardous waste. Industrial nonhazardous solid waste, and municipal solid waste. Virtually all wastes of Interest In exposure assessments will probably fit Into one of these categories. A key Is provided below which should be the starting point for the Stage III decision making. The Information In the key Is summarized In a flow chart In Figure 5. Use the key or Figure 5 to find the subsection that deals with the waste category to which the waste stream of Interest belongs. The text for each waste category Includes a general description of the waste and of the usual disposal practices, followed by a decision tree for estimating the quantity of the waste stream handled by each disposal practice. If the user Is unsure which category a particular waste belongs In, then the texts for several possible categories should be read. (In general, this problem Is likely to arise only when one Is trying to decide whether a given Industrial waste Is or Is not hazardous.) Two of the waste categories (Incinerator residues and POTW sludge) are the products of other treatment/disposal processes. For these wastes, the Input Information for Stage III will be provided by the Stage V output for wastes that were treated In POTWs or Incinerators. Appendix C contains Information on the waste disposal practices of the organic chemicals, plastics, and petroleum refining Industries that will be useful In Stage III. Appendix D provides Information on waste disposal that will aid the user In Stage III decisions. 16 17 FIGURE 5. KEY FOR DETERMING STAGE III STARTING POINT (in Sect. 2.3.3) The amounts of waste allocated to each disposal practice should add up to the original estimate of the total quantity of the waste stream, and the amounts of waste allocated to each site should add up to the total quantity disposed of at all such sites. However, If total figures and their component quantities were derived from separate sources, then the sum of the components may not equal the Independently-derived totals, and some numerical adjustments will have to be made. It Is recommended that the preliminary Stage III estimates be made for all applicable disposal practices, followed by Stage IV site-specific estimates for each disposal practice. At that point, all Stage III and Stage IV estimates can be compared and the necessary adjustments made. Note that Stage III can also be used as a screening tool for deciding whether or not exposure from a given disposal practice Is likely to be significant. Based on the Stage III estimate and knowledge of general emission factors (If available), some disposal practices may be judged Insignificant and not Investigated further. Note that the following key and Figure 5 separate hazardous and nonhazardous Industrial waste because the disposal sites and Information sources are usually different. The symbol W A will be used to designate the subject waste stream. Stage III Key Step 1. (a) If W A Is ash, scrubber water, or fly ash from an Industrial or municipal Incinerator, see Subsection (1), Incinerator residues. (b) If W A Is a wastewater treatment sludge from a POTW, see Subsection (2), POTW sludge. (c) If W A Is an Industrial waste stream (other than those listed above), go to Step 2. (d) If W A Is a resldentlal/commerclal waste stream (other than those listed above), go to Step 3. Step 2. (a) If W A Is an Industrial wastewater, see Subsection (3), Wastewater. (b) If W A Is a hazardous waste, as defined by the Resource Conservation Recovery Act (RCRA), see Subsection (4), Hazardous waste. (c) If W A Is neither (a) nor (b), see Subsection (5), Industrial nonhazardous solid waste. Step 3. (a) If W A Is a resldentlal/commerclal wastewater, see Subsection (3), Wastewater. (b) If W A Is a resldentlal/commerclal solid waste, see Subsection (6). Municipal solid waste (MSW). 18 (1) Incinerator residues . Background Information on the secondary products of Incineration that require further treatment/ disposal Is presented In this section, followed by a decision tree for estimating the probable disposal practice. (a) Background Information. Incineration of waste produces several kinds of releases besides the gases and particulates that are discharged directly Into the atmosphere. Residue composed of uncombusted and Inert material, fly ash collected by air pollution control equipment, and aqueous solutions from various sources are produced In varying quantities during controlled Incineration. These wastes may contain chemical substances that were In the Incinerated waste or were formed during Incineration. Unfortunately, there Is relatively little quantitative or qualitative Information on the fate of chemical substances In Incineration processes. It Is clear, however, that the following variables Influence the fate of toxic substances during Incineration and, hence, the amounts contained In the residuals: (1) physical and chemical characteristics of wastes; (2) design and operation of Incinerators; and (3) design and operation of pollution control equipment. These factors are discussed below for each product of Incineration. See Section 7 for additional Information on Incineration. Ash Is the residue remaining after Incineration and Includes both the bottom ash that remains In the combustion chamber and the fly ash that Is entrained In the exhaust gases leaving the Incinerator. In Incinerators with effective air pollution control equipment, most of the fly ash Is captured and must be disposed of to land. If Incineration results In complete combustion, the ash will consist almost exclusively of Inert matter. In practice, however, Incomplete mixing of wastes In the combustion chamber often occurs, resulting In Incomplete combustion. Table 2 gives typical characteristics of residue from municipal Incinerators. This table may provide useful generic data for a detailed exposure assessment In which the amount of a chemical left In the residue after MSW Incineration Is of Interest. For Instance, If the consumer product of concern Is paper containing a toxic chemical, then one can assume that no more than 1.8 percent of the residue will contain the subject chemical. In one study of municipal Incinerators, unburned combustibles ranged from 0.1 to 1.3 percent of the residue In four Incinerators; In the fifth Incinerator, 35.8 percent of the residue was unburned combustibles (Rubel 1974). (An overloaded furnace and the lack of proper agitation contributed to the high value.) Approximately 6 percent to 10 percent of the residue from municipal Incinerators Is water soluble and therefore subject to leaching If Improperly disposed of on land. Typical constituents In the water-soluble portion are presented In Table 3. The fly ash from municipal Incinerators Is also variable In composition, the organic matter ranging from 5 to 30 percent of the total. The chemical profile of fly ash from one municipal Incinerator Is given In Table 4. 19 Table 2. Characteristics of Municipal Incinerator Residue from Two Studies 3 Component Percent by welqht Ferrous metal 15.75 Magnetic flakes 3.80 Nonferrous metal 0.30 Glass over 1/4 Inch 9.48 Ceramics, stones 1.51 Cl Inkers 24.1 1 Ash, nonmagnetic 16.10 Combustibles Paper, wood, char 1.79 Putresclble (visual) 0.07 Bones, pits 0.03 1n conveyor water 27.06 TOTAL 100.00 Mater la I_Percent by weight (range) Metals 19-30 Glass 9-44 Ceramics, stones 1-5 CI Inkers 17-24 Ash (exclusive of other materials listed) 14-16 Organic 1.5-9 a The upper table Is based on the analysis from a 300-ton-per-day continuous feed incinerator. The data In this table are not meant to represent average or typical residue compositions, but can be used as a "first guess" in estimating residue composition. The lower table presents typical ranges of values for the various residual const Ituents. Source: Rubel 1974. 20 Table 3. Average Analysis of Water-Soluble Portion of Residue from Selected Municipal Incinerators 4 Constituent Batch-feed incinerator b Continuous-feed incinerator* 3 Hydrocarbon concentration 6.1666 (92.9132) 9.1666 (92.2602) Alkalinity 0.1156 (1.7418) 0.1865 (1.8771) Nitrate nitrogen 0.0004 (0.0060) 0.0003 (0.0030) Phosphate 0.0002 (0.0030) 0.0004 (0.0040) Chloride 0.1221 (1.8397) 0.0771 (0.7761) Sulfate 0.0813 (1.2250) 0.2447 (2.4629) Sodium 0.04675 (0.7044) 0.197 (1.9828) Potassium 0.04230 (0.6373) 0.048 (0.4831) Iron 0.0617 (0.9296) 0.015 (0.1510) a The water-soluble portion of residue is of interest because of the potential for water pollution from residue landfill sites by leaching. Most residue constituents listed in Table 2 may include a small water-soluble fraction. ^Percent by dry weight of total residue (water-soluble and Insoluble). Percent by dry weight of water-soluble portion in parentheses. Source: Rubel 1974. 21 Table 4. Chemical Analysis of Fly Ash Samples from a Municipal Incinerator 3 Component Percent by weight Or ga n 1 c 10.4 Inorganlc 89.6 Silica as SIO 2 36.1 Iron as Fe 203 4.2 Alumina as A 12 O 3 22.4 Calcium, as CaO 8.6 Magnesium as MgO 2.1 Sulfur as SO 3 7.6 Sodium and potassium oxides 19.0 a Based on samples from South Shore Incinerator In New York City. Other studies have shown that flyash can consist of an average of from 5 to 30$ organic matter and from 70 to 95$ Inorganic matter. Source: Rube I 1974. 22 Ash from sewage sludge Incineration Is generally composed of Inert matter. Ash from hazardous waste Incinerators, however, Is considered hazardous under RCRA regulations (see Section 2.3.3(4)) unless testing shows otherwise. Although most ash of this type consists largely of Inert compounds, the composition varies greatly. The relative proportion of fly ash to bottom ash depends on the waste composition and the design and construction of the hazardous waste Incinerator (Monsanto 1981). Incinerator ash Is generally disposed of on land; however, the exact disposal patterns for various ashes have not been determined. The bulk of municipal Incinerator ash Is probably disposed of In landfills, as Is bottom ash from sewage sludge Incineration (Walker 1979). Fly ash Is disposed of In either lagoons (with effluent treatment) or landfills (USEPA 1979a). Sludge Incineration ash Is sometimes used as a conditioning agent In sludge treatment processes. Bottom ash from the Incineration of hazardous wastes can be disposed of In landfills approved for hazardous wastes. The fly ash Is usually disposed of with the scrubber water, as explained below. Water Is used In various stages of the Incineration process and usually becomes contaminated with dissolved and suspended matter, requiring treatment prior to discharge (Rubel 1974). Scrubbers clean the combustion gases by carrying wetted fly ash (which may contain small amounts of organics) to the bottom of the scrubber. The fly ash and scrubber effluent are discharged to lagoons or sanitary landfills (USEPA 1979a). In hazardous waste Incineration facilities, the scrubber effluent (containing fly ash) Is combined with the quench water (which does not generally contain hazardous constituents), and treated on-site. This wastewater may contain chlorides, fluorides, sulfites, sulfates, phosphates, bromides, and bromates In addition to the particulate matter. Treatment normally Involves clarification, neutralization, and dilution. Suspended solids are often removed In on-site settling ponds. In sufficiently dry geographical areas, the scrubber wastewater can be treated In evaporation ponds, after which the sludge may be taken to a landfill for ultimate disposal. Alternatively, the wastewater may be discharged to a POTW providing that national and local pretreatment standards are met (Monsanto 1981). (b) Stage III decision tree for Incinerator residues. The Input to this stage will be the Information on amounts and subject chemical concentrations In Incinerator residues that Is the output of Stage V for Incineration (see Section 7.3). Because the amounts of toxic chemicals present In Incinerator residue will often be very low and because there Is little precise Information on disposal practices for these wastes, the user should carefully evaluate the expected loadings before expending considerable effort to proceed with the method. One or all residual products may be discounted as unworthy of further consideration as a potential source of human exposure. 23 In this decision tree, the user evaluates the available Information on the waste disposal practices used for Incinerator residues for the various waste categories. Then the amount of the subject waste disposed of by each likely practice Is estimated. Step 1 . Determine which disposal practices are used for disposal of Incinerator residues. The available literature suggests that landfills and surface Impoundments are the only practice currently used for disposal of bottom ash. Quench waters and scrubber waters may be treated by a variety of standard wastewater treatment methods, Including lagoons; treated effluent may be discharged directly to surface waters, to POTWs, or to evaporation ponds. The sludge from storage lagoons Is generally landfilled. Step 2 . Considering the available Information, estimate the percentage of Incinerator residues that will be disposed of by each practice. The following guidance Is based on limited Information. It should be used only If more specific Information Is not available. • Bottom ash. In the absence of quantitative Information to the contrary, assume that all bottom ash from municipal and sewage sludge Incinerators Is landfilled. Assume that all bottom ash from Industrial Incinerators Is also landfilled, unless the available Industry-specific documents on waste disposal practices Indicate otherwise (see Table 8 under "Hazardous Waste" (Subsection (4)). For ashes produced from Incineration of Industrial hazardous waste, assume ultimate disposal Is In a landfill designed for hazardous waste, unless the above-mentioned documents suggest differently. • Fly ash. The Information on fly ash disposal Is so sparse that any assumptions may be suspect. More fly ash than bottom ash Is probably treated or disposed of In lagoons. In the absence of data to the contrary. It may be assumed that 50 percent Is treated In lagoons and 50 percent Is transported directly to landfills for disposal. A significant portion of the fly ash treated In lagoons may require ultimate disposal In a landfill. Assume that fly ash from Incineration of hazardous wastes Is treated In lagoons or landfills designed for hazardous wastes (see Subsection (4)). 24 • Scrubber water and other wastewaters. For Incinerator ash from POTWs (see Subsection (2)) and municipal Incinerators, assume that the water Is treated by the POTW. For Industrial Incinerators, assume that the same proportion Is treated on-site as for other wastewaters of the same Industry (see Subsection (3), Wastewater). (2) POTW sludge . A description of the sources, characteristics, and disposal practices associated with municipal wastewater treatment sludge (POTW sludge) Is presented here, followed by a decision tree for estimating the amounts of sludge handled by the various available disposal options. (a) Background Information. The process of wastewater treatment produces a sludge composed of the materials that settled from the raw wastewater (such as sticks, organic solids, and rags), as well as solids actually generated In the wastewater treatment process (such as excess activated sludge or chemical sludge produced by advanced treatment). Some typical constituents of sludges are given In Table 5. In general, the sludge generation rate Increases with Increasing levels of wastewater treatment, from primary to advanced wastewater treatment; typical sludge generation rates as a function of total wastewater flow and treatment level are presented In Table 34 In Section 6. When sludge Is withdrawn from treatment processes, It Is composed largely of water (up to 97 percent) (Culp 1979), some of which Is removed In subsequent treatment. The primary purpose of sludge treatment processes Is to separate large amounts of water from solids; treatment may Include the following: • Conditioning - treatment of the sludge with chemicals or heat so that the water can be easily separated. • Thickening - separation of waste by gravity or flotation. • Dewatering - further separation of water using vacuum pressure or drying processes. • Stabilization - digesting the organic solids so that they can be handled or used as solid conditioners without causing a nuisance or health hazard. • Reduction - reduction of solids by wet oxidation processes or Incineration. See USEPA (1980g) for an In-depth description of various sludge treatment and disposal methods. The final water content of treated sludge will vary depending on the treatments used. The only treatment 25 Table 5. Average Characteristics of Sewage Sludge Materia 1 Combustibles (%) Ash (?) BTU/lb Grease and scum 88.5 11.5 16,750 Raw sewage sol 1 ds 74.0 26.0 10,285 Fine screenings 86.4 13.6 8,990 Ground garbage 84.8 15.2 8,245 Digested sewage solids and ground garbage 49.6 50.4 8,020 Digested sludge 59.6 40.4 5,290 Grit 30.2 69.8 4,000 Source: Rubel 1974. 26 process considered In detail In this volume Is reduction by Incineration, which usually requires a moisture content of less than 70 percent for the combustion to be self-sustaining. (See Table 37 In Section 7 for Information on the typical moisture content of sludges treated by Incineration.) Sludge treatment and disposal can be a source of exposure to chemical substances because of the tendency of sludges to accumulate metals and nonvolatile organics that were present In the wastewater. An EPA study of toxic chemicals In POTW wastewaters and sludges (Burns and Roe 1982) has reported that numerous priority pollutants have been found In POTW sludges at much higher concentrations than those measured In the Influent wastewater (see Tables H-4 and H-7 In Appendix H). The major disposal practices used for POTW sludges and the amounts of sludge handled by each practice are given In Table 6. Estimates vary, however, depending on the method of estimation; for example, some authors consider lagoons to be a disposal option, while others treat them as storage facilities prior to ultimate disposal by landfilling. Similarly, Incineration Is usually listed as a disposal practice (rather than a treatment practice), with little consideration given to the ultimate disposal of the residues. For the purposes of this volume, the Needs Survey (Exhibit H-l In Appendix H) coupled with the Surface Impoundment Assessment (SIA) data base (Section 5) and surveys of municipal sludge Incinerators will generally be sufficient to determine both disposal practices and the general locations of sludge Incinerators and lagoons. There are no good sources of data on exact locations of landspreading sites or landfills receiving POTW sludges, although reasonable assumptions might be made based on the fact that It Is expensive to haul sludge great distances. The ultimate fate and exposure from sludge that Is ocean-disposed or distributed for marketing will not be explored In this method. Neither will such uncommon treatment practices as composting, pyrolysis (thermal decomposition In the absence of oxygen), and coincineration be discussed. As Table 6 Indicates, all of the uncommon sludge disposal practices combined (Including disposal In lagoons) handle only 12 percent of the POTW sludge generated. (b) Stage III decision tree for POTW sludge. The user will need the following Information on the subject sludge from the Stage V output of the POTW analysis (Section 6.3): amount and sources of sludge (Including geographic location), possible concentrations of chemical substances, and other physical/chemical characteristics such as the moisture content. Using this Information and Steps 1 and 2 below, the disposition of the sludge to the various disposal methods can be estimated. 27 Table 6. Current Nationwide Disposal Practices for POTW Sludge Disposal Method Percentage, by weight, I980 a Ocean disposal 4 1nclneratlon 27 b Landspread on non-food chain land 12 Landspread on food chain land 12 Landf 11 1 15 b Distribution for marketing 18 Other 12 C a Based on most recent estimates (personal ccmmuntcatlon with M. Flynn, EPA Office of Solid Waste, September 24, 1981). b Based on 1978 estimates, the bulk of the ash Is ultimately disposed of In landfills (Walker 1979). If this Is still true, the landfilled estimate Is too low. c Based on 1978 estimates, the bulk of this category Is probably disposed of In surface Impoundments (Walker 1979). 28 Step 1 . As a first cut, look at Table 6 to determine the major disposal options and the quantities of sludge handled by each practice. In a very general, nationwide exposure assessment, the figures In Table 6 may suffice. For accurate Information based on site-specific data, however, go to Step 2. Step 2 . If a detailed exposure assessment Is required, examine site-specific data In order to estimate the amount of the subject sludge disposed of by each practice. A detailed exposure assessment that evaluates exposure on a local or regional basis will require Information that was compiled by the Needs Survey (Section 6 and Exhibit H-l In Appendix H), which contains site-specific data for each POTW In the U.S. Therefore, an accurate Stage III estimate of sludge disposal practices will be based on the site-specific data obtained In Stages IV and V of the POTW evaluation (Sections 6.2 and 6.3). This Is a case where Stage III cannot be estimated until Stage IV has been completed. One complete Needs retrieval, providing both the site-specific data needed for Stage IV and the summary statistics needed for Stage III, should be conducted, as outlined In Section 6. The Needs Survey contains detailed Information on the sludge treatment/disposal practices at each POTW. Table H-8 In Appendix H lists all of the sludge treatment parameters used In the Needs Survey data base. Summary statistics on the total wastewater flow produced by each wastewater treatment process and treated by sludge disposal practice are available from Needs. The user can apply the sludge generation factors given In Table 34 In Section 6 to convert these flows to volumes of sludge. The final output of Stage III should Include the total sludge volume, concentration of chemical substance, and other physical/chemical characteristics of the sludge disposed of by each practice of Interest In the study area. The uncertainty In the quantitative output of this step depends on the accuracy of the site-specific Needs estimates and the sludge generation factors. (3) Wastewater. This section contains the Information necessary for determining how much of a given commercial, residential, or Industrial wastewater will be treated at a municipal wastewater treatment plant (POTW). Note that Industrial wastewater treated on-site Is not covered In this volume; rather this source Is Included as a point source In Section 6.3 of Volume 2 (ambient exposure scenario). A general discussion of wastewater Is presented first, followed by the decision tree. 29 (a) Background Information. Wastewater Is generally treated and disposed of by entirely different practices from those used for solid waste. Wastewaters can be grouped Into five categories based on their origin: residential, commercial. Industrial, stormwater, and groundwater. Only the first three categories are true waste streams. Exposure to chemical substances In stormwater Is considered In the ambient exposure assessment volume (Volume 2). Groundwater seepage Into sanitary sewers results when groundwater enters sewer pipes through cracks or loose joints. Such seepage Is most prevalent In older sewer systems and does not generally contribute significant levels of toxic chemicals to municipal wastewaters. Therefore, this process Is not treated explicitly In any of the volumes of this series. A brief description of residential, commercial, and Industrial wastewaters and the treatment/disposal practices most commonly applied to them Is presented below. Residential wastewater comprises all wastes entering sewers from homes. The primary source of chemical substances In residential wastewater Is probably consumer products that are washed Into drains from bathtubs, sinks, and washing machines. Chemicals may also leach from components of the plumbing system. Residential wastewater Is generally disposed of through municipal sanitary sewers or on-site septic tanks/leachflelds. Some residential wastewaters are discharged directly to land or surface waters. Commercial wastewaters originate from office buildings and nonmanufacturing Industrial facilities. Although much of this waste Is similar In composition to residential waste, significant levels of toxic chemicals may be contributed by such Industrial sources as film developers, testing laboratories, service stations, and dry cleaning establishments. Some commercial wastes are treated on-site, others are routed to POTWs, and some are discharged directly to surface waters. The annual Needs Survey conducted by the Priority Needs Branch of the EPA Office of Water Program Operations (see Exhibit H-l In Appendix H) does not give a breakdown on the relative contributions of residential and commercial wastewaters to POTWs; these two types are combined under the "domestic" category. Industrial wastewaters originate at manufacturing or processing facilities and may consist of large volumes of water used In manufacturing and processing Industrial products. Industries also produce sanitary and nonprocess wastewaters. Industrial wastewaters may be discharged either directly to surface waters with or without prior on-site treatment, or Indirectly (l.e., to POTWs). (The distinction between direct and Indirect discharge should be borne In mind throughout the following discussion.) Industrial wastewaters may also be treated by other means, such as on-site septic tanks/leachflelds, Injection wells, or land treatment, and not discharged to surface waters at all. Special 30 effluent guidelines governing the quality of effluents discharged to surface waters have been developed for the 21 major Industries Identified by the EPA as producing effluents containing significant amounts of toxic substances; these Industries are listed In Table 0-8 In Appendix D. In addition, pretreatment standards regulating the quality of effluent discharged to POTWs are being developed for these Industries. Of the various disposal practices used for wastewaters, only the disposal by municipal collection and treatment systems, Injection wells, and land treatment are considered In detail In this volume. Exposure to chemical substances via Industrial and commercial on-site wastewater treatment with discharge to ambient waters (1.e., direct discharge) Is covered by Volume 2 of this methods development series. The potential for exposure to chemicals as a result of leaching from septic tank waste Is not discussed In this report. Nationwide, about 73 percent of wastewaters treated by POTWs are of domestic (residential or commercial) origin, the balance being contributed by Industrial plants (USEPA 1981e). Seventy percent of the U.S. population Is served by POTWs (see Table 7). The extent of Industrial wastewater treatment by POTWs varies, however, ranging from treatment plants that receive no Industrial effluents to plants that are operated jointly by a sewage authority and an Industry, treating a large volume of Industrial wastewaters. The degree to which Industrial wastewaters are discharged to surface waters Indirectly (via POTWs) depends on many factors, Including the treatment capability of the local POTW, the nature of the industrial wastewaters, cost considerations on the part of both the Industry and the sewage authority, and federal and state policy and regulations. The EPA has developed extensive documentation for the Industrial wastewater treatment practices of the 21 major Industrial categories (see Volume 2, Section 6.3 of this methods development series). These studies provide useful generic data on Industries that can be used for exposure assessments when site-specific Information Is not available. As a result of the National Pollution Discharge Elimination System (NPDES), however, site-specific Information Is available for all facilities that discharge to surface waters. These data are available In computerized form through several EPA data bases Including the Permit Compliance System (PCS) and the Industrial Facilities Discharge File (IFD), and can be used to extract both generic Information on Industries and site-specific Information on permit holders. (b) Stage III decision tree for wastewater. Ideally, the Input to this stage will be Stage II estimates of wastewater flow, concentration of the subject chemical In the wastewater, and related Information on the source of the wastewater. In some cases, however, the user may know only the quantity of the subject chemical discharged to 31 Table 7. Populations Served by Wastewater Treatment Types Type of Number of Number of Percent of treatment _ persons (xlO^j _ POTMs _ total population No treatment 67.1 0 30.0 Treatment but no discharge 3.6 1,361 1.6 to surface waters Preliminary 2.3 272 1.0 Primary 37.3 3,343 16.6 Secondary 62.7 7,852 28.0 Advanced secondary 47.5 2,443 21.2 Tertiary 4.9 251 2.1 Source: USEPA 1981e. 32 wastewater from a given source. In this stage, available Information will be used to determine whether the subject wastewater will be treated at a POTW, based on the source of the wastewater. Then the user will estimate the actual amount of wastewater likely to be treated at POTWs. An additional step for estimating the concentration of the chemical In the wastewater Is given for cases where concentration Is needed but not provided by the Stage II output. Step 1 . Estimate the proportion of the subject waste stream that will be disposed of by POTWs. (See l.a for domestic wastewater and l.b for Industrial wastewater.) a. Domestic wastewater . For a nationwide exposure assessment It can be assumed that 70 percent of the U.S. population Is served by POTWs (Table 7). For assessments of regional or statewide scope, consult the published annual summaries of the technical Needs Survey data base (USEPA 1981e). This presents, among other things, the percentage of the resident population In each state that Is served by POTWs and the total domestic flow treated by POTWs In each state; these data are also summarized In Appendix D, Tables D-l and D-2. For detailed assessments where greater geographic resolution Is required, a computerized retrieval from the Needs Survey data base Is recommended (see Exhibit H-l In Appendix H). This provides the same kind of data discussed above for POTWs within small geographic areas (e.g., county, Congressional district, sewer district). This retrieval can be conducted so as to satisfy the requirements of the Stages IV and V decision trees for POTWs as well, by requesting. In the same operation, Information on the parameters listed In those decision trees (see Sections 6.2 and 6.3). b. Industrial wastewater. The likelihood that a given Industrial wastewater will be treated at a POTW depends on the Industry and the local sewage authority. Industrial wastewaters may be treated by a POTW provided that the sewage authority has given the plant a permit to discharge Indirectly. Industries that are among the 21 major Industries (see Table D-8 in Appendix D) must meet pretreatment standards In order to be permitted to discharge to a POTW. When site-specific data are not required (as In the case where the exposure assessment Is general In nature), the wastewater disposal practices of the Industry as a whole (or for the appropriate subcategory) can be used as surrogate data If the Industry has been studied by the Effluent Guidelines Division (EGD) of EPA. This Information can 33 be obtained from various publications, such as the development documents series, for the 21 major Industries. (See Section 6.3 of Volume 2 for a list of relevant EGD publications.) for exposure assessments where site-specific Information Is required, however, a computer retrieval from the IFO file Is recommended (see Exhibit H-2 of Appendix H). This will provide Information In a single operation for both Stages III (for wastewater In general) and IV (for POTWs); refer ahead to Stage IV, Step 1 for POTWs (Section 6.2) for guidance. Step 2 . Estimate the concentration of the chemical of Interest In the wastewater treated by POTWs, If It Is not already provided by available Information. (See 2.a for domestic wastewater and 2.b for Industrial wastewater.) a. Domestic wastewater. Concentration of the subject chemical In domestic POTW Influent can be determined using Tables D-l and D-2 In Appendix D. Which table to use depends on the type of data that was originally used (probably In Stage II) to determine the total mass of the subject chemical In all domestic wastewaters. If this estimate was based on the per capita use of a product containing the subject chemical (e.g., mass of product used per person per day), then Table D-l should be used, since It Is based on population data. If the estimate was based on the average concentration of the subject chemical found In all domestic wastewaters (e.g., mg chemical per liter of wastewater), then Table D-2 should be used, since It represents directly the total amount of wastewater treated at POTWs. Data from Tables D-l and D-2 can be used In the following equations: P = A x B (2-1) F = P x G w (2-2) Q = P x G c (2-3) C = Q v f (2-4) where P = population contributing the subject wastewater to POTWs A = population served by POTWs (from Table D-l) B = fraction of population using a product containing the subject chemical F = flow of subject wastewater (volume/day) G w = per capita wastewater generation (from Table D-2) (Volume per cap./day) G c = per capita disposal of subject chemical (mass per cap./day) Q = total quantity of subject chemical routed to POTWs (mass/day) C = concentration of subject chemical In waste stream (mass/volume). 34 For a detailed assessment requiring geographic resolution beyond the state level, a computerized retrieval of the parameters A and G w from the Needs Survey data base Is recommended as Input to Equations 2-1 through 2-4. b. Industrial wastewater. The total mass of the subject chemical released to wastewater should have been determined In Stages I and II. The proportion of this chemical treated by POTWs will also have been provided by Stages I and II, or else by Step 1 above. The concentration of the subject chemical In Industrial POTW Influent can then be calculated as follows, If not already provided by the Stage II Information sources (Equation 2-5). C = M (2-5) F where C = concentration M = mass of chemical treated at POTWs F = wastewater flow to POTWs from subject Industry (4) Hazardous waste. Background Information on hazardous waste Is presented below, followed by the Stage III decision tree for allocating hazardous wastes to likely disposal methods. (a) Background Information. Hazardous waste Is defined by Title 40 of the Code of Federal Regulations (40 CFR Part 261). To be considered hazardous, a waste must be named In the list of specific hazardous waste streams and chemicals provided In the cited regulation, or It must exhibit one or more of certain specific characteristics which Include Ignltabl11ty, corrosivity, reactivity, and toxicity. The definition excludes household waste, agricultural waste returned to the soil, and mining overburden returned to the mine site. It also excludes all wastewater discharged directly or Indirectly to surface waters, since this Is regulated by other legislation. (It should be noted, however, that, although hazardous waste Is considered a solid waste by EPA definition, a large part of It Is physically In the liquid state.) About 20 percent of the total of 41.2 million wet metric tons (kkg) of hazardous waste generated yearly Is known to be specifically Included In the EPA hazardous waste list (USEPA 1980f). 35 Permits are required for the storage, treatment, and disposal of hazardous waste under Subpart C of the Resource Conservation and Recovery Act (RCRA). Permitting authority may be ceded to the state If EPA determines the state's hazardous waste regulatory program to be "substantially equivalent" to that of EPA (40 CFR Part 123.128). Identifying the agencies that have Jurisdiction over the disposal of a subject waste will facilitate the assessment procedure, since they may be Important sources of relevant data (as discussed below). It is also Important to be familiar with the regulations themselves, since they may dictate performance standards or deslgn/operatlonal features of hazardous waste disposal facilities; In the absence of reliable site-specific data, these requirements can be used as Input parameters for various stages of the assessment (assuming compliance with the regulations). Regulations also Influence the generation and disposal patterns of hazardous waste by their effect on the cost-benefit ratio of disposal options. The most recent hazardous waste regulations were promulgated In July 1982 (USEPA 1982b). Nationwide trends relating to the generation and disposal of such waste will be affected by any changes In these regulations. Therefore, many estimates and assumptions Incorporated Into this volume may have to be modified In the future. Almost all Industries generate hazardous waste, but the chemical Industry Is the major source, contributing 60 percent of the total (USEPA 1980f). Other major contributors Include the primary metals, petroleum and coal products, and fabricated metal products Industries. Generation of hazardous waste within a region reflects the particular makeup of Industry In that region. About 23 percent of hazardous waste Is treated off-site by commercial hazardous waste handlers (USEPA 1980b). In general, half of all hazardous waste goes to surface Impoundments, about 40 percent to landfills, and the rest to Incinerators, land treatment, and Injection wells. Some treatment methods produce new hazardous waste requiring ultimate disposal; these Include Incineration producing toxic ash and wastewater treatment producing toxic sludge. Possible disposal methods for the various types of hazardous waste are summarized In Table 8. In some cases, e.g., Iowa and Kansas, manufacturers apply to the state for permission to dispose of their hazardous waste and are directed where to do so. Nevertheless, about 9 percent of the nation's hazardous waste may be Improperly diverted to municipal landfills not designed for Its acceptance (Van Noordwyk 1980). This practice may be especially common In areas with few or no permitted hazardous waste disposal sites (USEPA 1980b). 36 Table 8. Hazardous Waste: Possible Disposal Methods Solid Waste La nd fill Inclneratlon a SIudge LandfI 11 Inclneratlon 3 Landspread Surface Impoundment Injectlon we I I POTW Liquid Waste LandfI I I Incineration 3 Surface Impoundment LandspreadIng Injection we I I a For ultimate disposal of Incinerator ash. see Section 2.3.3(1). 37 Major sources of data on hazardous waste generation patterns Include the various RCRA background documents, available from EPA, and the series of Industrial hazardous waste assessment reports produced for the EPA Office of Solid Waste (OSW) (see Table 9). Additional sources of Information are the reports on waste generation Issued by a number of Individual states. A list of state reports obtained In this study Is given In Appendix B, Exhibit B-l. For additional Information, the state agencies should be contacted; state solid waste agencies are listed In Appendix D, Table D-3. A major source of Information on both generation and disposal of hazardous waste Is the Hazardous Waste Data Management System (HWDMS). This data base Is maintained by the EPA State Programs and Resource Recovery Division of the Office of Solid Waste (OSW) and contains data from RCRA permit applications. See Appendix D, Exhibit D-l for a discussion of HWDMS. A recent summary of the population of hazardous waste sites listed In HWDMS by treatment/storage/dlsposal method Is given In Appendix D, Table D-7. In addition, several states maintain their own lists of permitted hazardous waste disposal sites. (b) Stage III decision tree for hazardous waste. The Input to this stage will be the volume or mass, chemical concentration, source, and other physical/chemical Information for the subject waste stream, derived from the output of Stage II. The following references will be useful: • RCRA background documents • All OSW Industrial waste disposal assessments (see Table 9) • Any relevant state surveys or reports (see Appendix D, Table D-3 and Appendix B) • HWDMS data base • Appendices C and D to this report. The user will evaluate available Information on the disposal practices used by the Industry that generates the waste as well as the characteristics of the waste. This Information Is used to estimate the amount handled by each disposal practice. Step 1. Determine the probable distribution of the subject waste stream among disposal types, based on generic data. Compile all relevant estimates from each reference source above. List available estimates, and decide which to use based on how recent the data are, the estimated reliability of the data collection methods, or other factors. If appropriate, estimates from different sources can be combined and averaged. Estimates thus obtained may be sufficient for 38 Table 9. OSW Industrial Hazardous Waste Assessment Reports 1ndustry SIC Prepared by Date EPA no. NT I S no. Metals mining 10 Midwest Research Institute 9/1976 SW 132c PB 261 052 Text!les 22 Versar, Inc. 6/1976 SW 125c PB 258 953 Inorganic chemicals 281 Versar, Inc. 3/1975 SW 104c PB 244 832 Rubber and plastics 282,30 Foster D. Snell, Inc. 3/1978 SW 163c.1-4 PB 282 070-073 Pharmaceutlea 1s 283 Arthur D. Little, Inc. 1976 SW 508 PB 258 800 Paint and allied products 285 Wapora, Inc. 9/1975 SW 119c PB 251 669 Organic chemicals, pest 1c1des, exp 1 os 1ves 286,2879 2892 TRW Systems 1/1976 SW 118c PB 251 307 Petroleum refining 2911 Jacobs Engineering Co. 6/1976 SW 129c PB 259 097 Petroleum re-reflnlng 2992 • • • 1977 SW 144c PB 272 26 7 Leather tanning and 3111 SCS Engineers, Inc. 11/1976 SW 131c PB 261 018 finishing Metal smelting and refining 33 CaIs pan Corp. 4/1977 SW 145c.1-4 PB 276 169-1 72 Electroplating and metal 3471 Battelle Columbus Labs 9/1976 SW 136c PB 264 349 finishing Special machinery 355,357 Wapora, Inc. 4/1977 SW 141c PB 265 981 manufacturIng Electronics components 367 Wapora, Inc. 1/1977 SW 1 40c PB 265 532 manufactur 1 ng Storage and primary 36 91,3692 Versar, Inc. 1/1975 SW 102c PB 241 204 batteries Source: Van Noordwyk 1980. 39 exposure assessments that do not require great depth of detail In the disposal setting, for more detailed or site-specific assessments, proceed to the following steps. Step 2 . Compile the names and locations of all facilities receiving the subject waste stream. This may be accomplished by conducting an HWDMS retrieval for the geographic area of Interest (see Appendix D, Exhibit D-l). Use the Standard Industrial Classification (SIC) code for the Industry that generates the subject waste stream, as well as the SIC code for commercial (off-site) waste handlers (4953) or the commercial "tag" mentioned In Exhibit D-l. Step 3. Confirm or correct the gross estimates from Step 1 using HWDMS data. The retrieval conducted In Step 2 provides only facility names and locations. In order to determine the specific treatment types employed at these locations, consult the complete HWDMS printout of permit application data; this must be consulted manually at the EPA Office of Solid Waste. It lists the treatment, storage, or disposal practices used at a given hazardous waste facility (process code), as well as the proposed capacity, arranged by location (zip code). Use this Information to confirm or correct the gross estimates from Step 1. For example, If most generators of the subject waste have on-site hazardous waste disposal capacity, It can be assumed that all of their waste stays on-site and Is treated by the practice listed In their permit application. Step 4. If data collected thus far are Insufficient, skip ahead to Stage IV for the disposal practices of Interest; Information obtained there may be applied to Stage III. In any case, after Stage IV Is completed, return to Stage III and make any necessary adjustment. If the Stage IV procedures do not provide the desired Information, estimate the quantity of waste handled by each applicable disposal practice based on available Information on the waste disposal practices of similar Industries or on the relative proportions of different types of hazardous waste disposal facilities available In the area. Note that hazardous waste may be diverted to facilities not permitted for It. The output of this step will be a list of the disposal practices likely to receive the waste stream of Interest and estimates of the amounts of the waste disposed of by each practice In units of mass/year. 40 (5) Nonhazardous Industrial solid waste . This category Includes all nonhazardous (l.e., not designated as hazardous by RCRA) solid waste materials from factories, processing plants, and other manufacturing enterprises. It also Includes sludges and liquid wastes not discharged to sewers. General Information on this waste category Is presented In (a), followed by the Stage III decision tree (b). (a) Background Information. A total of 56.3 million metric tons (kkg) of solid waste (hazardous and nonhazardous) are generated annually (Table 10). The largest generators are the fabricated metals, chemical, nonelectrical machinery, rubber, and plastics Industries. A total of 8.4 million metric tons of Industrial sludge are generated annually (Table 11); 90 percent of this Is produced by three sources, the nonelectrical machinery, chemical, and textile mills Industries. The nonelectrical machinery Industry alone generates 50 percent of the total. Industrial wastes are difficult to quantify because they are usually of a unique character, peculiar to a specific Industry and often to a specific plant. Typical wastes Include spent solvent; discharged products, spills, and sweepings; unwanted by-products, fractions, or residues from distillation or other processes; wastewater and cooling tower sludges; and empty containers. Solids are generally landfilled or Incinerated. Liquids may be Incinerated, kept In surface Impoundments, or landspread; they may also be drummed and landfilled, provided that the landfill possesses a synthetic liner and a leachate collection and recovery system (40 CFR Parts 264-265). Sludges may be treated by any of these practices, as well as by ocean dumping; occasionally. Industrial sludges are sent directly to a POTW or are sold as soil conditioner or fertilizer. Residue resulting from Incineration Is discussed In Section 2.3.3(1). Possible disposal practices for Industrial wastes are summarized In Table 12 . Treatment, storage, and disposal of nonhazardous solid waste are regulated under Subtitle D of RCRA. In general, guidelines and regulations governing nonhazardous solid waste are less stringent than those governing hazardous waste. To date, the disposal of nonhazardous Industrial waste has received relatively little attention. Consequently, very few data quantifying the relevant waste generation and disposal practices are available. Because disposal problems are handled by the Individual firms, the exact practices used for disposal are as varied as the Industries themselves. In addition, wastes are often disposed of on-site, making assessment of the disposal practices more difficult to quantify. 41 Table 10. Industrial Solid Waste Production 3 SIC Code 1ndustry Metric tons per year 22 Textlle mill products 1,642,105 23 Apparel 2,412,150 24 Wood products 4,581,679 25 Furniture 1,004 , 846 26 Paper and allied products 2, 134,034 28 Chemicals and allied products 6,817,586 29 Petroleum 203,897 30 Rubber and plastics 5,237,397 31 Leather 1,957, 157 32 Stone, clay 3,443,644 33 Primary metals 3, 152,288 34 Fabricated metals 8,801,146 35 Non-electrical machinery 5, 725,367 36 Electrical machinery 4,058, 142 37 Transportation equipment 3,728,091 38 Professional and scientific Instruments 805,62 8 39 Miscellaneous manufacturing 572,971 a lncludes hazardous waste; excludes sludge. Source: USEPA 1980b. 42 Table 11. Sludge Generation 3 by Manufacturing Industries SIC Code 1ndustry Metric tons per year 22 Textlle-ml11 products 1, 147,334 23 Apparel 0 24 Wood products 0 25 Furniture 0 26 Paper and allied products 6,441 27 Printing, publishing 0 28 Chemicals and allied products 1,964,814 29 Petroleum 363 b 30 Rubber, plastics 45,451 31 Leather 0 32 Stone, clay 5,897 33 Primary metals 418,673 34 Fabricated metals 70,852 35 Non-electrlea 1 machinery 4,404,002 36 Electrical machinery 0 37 Transportation equipment 277,966 38 Professional and scientific Instruments 0 a lncludes hazardous sludge. b Estlmate based on only one observation. Source: USEPA 1980b. 43 Table 12. Nonhazardous Industrial Solid Waste: Disposal Methods Solid Waste LandfI I I IncInerat!on a SIudqe LandfI I I Inc IneratIon 3 Landspreading Surface Impoundment POTW b Inject ion welI Ocean Liquid Waste, to Land LandfI I I Inclneration 3 Surface impoundment Inj ection welI Landspreading 3 For ultimate disposal of incinerator residue, see Section 2.3. 3(1). b This practice is not very widespread and will not be examined in detail In the methodology. 44 Since hazardous waste disposal Is relatively well documented, and nonhazardous waste Is frequently disposed of In hazardous waste streams. It may be assumed that. In some cases, they are disposed of In a roughly similar fashion. The sources of Information on Industrial waste generation and disposal are the same as for hazardous waste, which are described In Section 2.3.3(4). (b) Stage III decision tree for nonhazardous Industrial wastes. The same basic procedure Is used to determine the likely disposal practices for nonhazardous Industrial waste as for hazardous wastes except that there Is less Information on nonhazardous waste. The following sources of Information should be used: • RCRA background documents (see Subsection (4)) • All OSW hazardous waste assessments (see Table 9) • Any relevant state surveys or reports (see Appendix D, Table D-3, and Appendix B) Step 1 . Determine the probable distribution of the subject waste stream among disposal types based on readily available Information. Compile all relevant estimates from each reference source above. Most of the data In these surveys may pertain specifically to hazardous waste; In the absence of better Information, assume that nonhazardous waste Is treated similarly. List all available estimates and decide which to use based on how recent the Information Is, the reliability of the data collection methods, or other factors. If appropriate, estimates from different sources can be combined and averaged. Step 2 . Determine whether It Is likely that the subject waste stream Is co-dlsposed with hazardous waste. Co-disposal Is likely when hazardous and nonhazardous wastes are generated simultaneously or In a manner likely to result In their mixing; It Is then often not economically advantageous to separate them. This Information may be deduced from Information compiled In Stages I and II. If It appears likely that the waste will be diverted to a hazardous waste stream, conduct an HWDMS retrieval as described In Section 2.3.3(4) for hazardous waste (see Appendix D, Exhibit D-l). 45 Step 3 . If data collected thus far are Inadequate, skip ahead to Stage IV; Information obtained there can be applied to Stage III. In any case, after Stage IV Is completed, return to Stage III and make any necessary adjustments. Step 4 . If the Stage IV procedures do not provide the desired Information, estimate the quantity of waste handled by each disposal practice based on the waste disposal practices of similar Industries, or on the relative proportions of different types of disposal facilities available In the area (see Section 2.3.3(4) and Stage IV). The output of this step will be a list of the disposal practices likely to be used for the subject waste and estimates of the amounts disposed by each practice In units of mass/year. The uncertainty In these estimates may be high as a result of the paucity of Information on nonhazardous waste disposal practices. (6) Municipal Solid Waste (MSW). This category Includes all nonlndustrlal solid waste: residential, commerclal/lnstltutlonal, constructlon/demolltlon, and agricultural. General Information on MSW Is given In (a) followed by the Stage III decision tree In (b). (a) Background Information. The typical composition of MSW Is given In Table 13. A description of various types of MSW follows: • Residential (domestic). This Includes all wastes generated by normal household activities, Including food wastes, paper, clothing, and manufactured objects, as well as yard waste resulting from lawn and garden care. It also Includes wastes from campgrounds, public access areas, and roadside rest stops. Toxic substances may enter these waste streams by means of household cleaning chemicals; paints; lawn and garden chemicals; and as components of manufactured products such as plastics, batteries, dyes In clothing, or paper. Nationwide, about 90 percent of residential waste Is landfilled and the rest Is Incinerated (Lacombe 1977). Wastes are hauled by public or private haulers or transported by homeowners to municipal disposal sites. • Commerclal/lnstltutlonal. These wastes are generated from a variety of sources, such as: shopping centers, restaurants, hotels, schools, hospitals, nursing homes, and automobile service stations. They also Include street sweepings and refuse from litter baskets. Generators of commercial waste Include the following employment groups: transportation, communications, and utilities; wholesale and retail trade; finance. Insurance, and 46 Percent Moisture _ Analysis (percent dry weight) __ of all (percent Non- refuse by by Volatile ccmbus- Component _ weight _ wel ght) _ matter _ Carbon _ Hydrogen _ Oxygen _ Nitrogen _ Su I fur _ 11 b les o O 00 m o CN ___ o CN •*3- in O m in O O o m CN ON • • • • • • • • • • • • • • • • • • • • • VO — VO 00 00 o o o VO r- CN in CN CN vO o Qv a o CN (N K vO Cv r* CN OtOlOIOlTvlOO • • O O — ITi (SlO (NOOOOO'3-O • • rf — o • •••••••••••••• •• OOOOOOOCN ooooo oo in o in m (N CN O O CN o • • o —> vO — in o m o • • • • • • • • • • • • • • • • • • • • • • • • o O CN CN CN o o • • CN o o o o o • • • o m (N o — m • vo CN CN CN o TT 00 CN CN — 00 TJ- • • • • • • ^3” CN — — av in — • CN in 00 — in 00 CD — O o o CN Tj- TT — CN — m in — CN — CN ooooovvooo^rcNP-'K'ivooovoin • •••••••••••••• invovoininioooo^o^vo^cNCN — • • vO CN K\ O O in in • • • • o o o ^3- in in m in O O Ov — O VO vo o ao vO o O • • • • • o m CN O o O O vo ao in o vO in vO o o ao 00 *3- in tr vO vo vO in m CN — P^ CN CN VO a • • m • CN o • • CO vo CN • • in *3- o • • • • • • • s • • o • vo in • • in m n* — • m • o o • 00 o O in in o vO P^ 00 — VO O O in o o o O o © • • • • • (Jj CN CN — — in o O O o o O — o o CN 00 vO o d) o TT — L. o Vi in rr 4- XL in in o in © 4- ~0 JO in U (0 in oc < s 5 CE 3 CD 51 STAGE III OR STAGE IV *IF SITE SPECIFIC ESTIMATES OF ENVIRONMENTAL RELEASES OUTPUTS AS NECESSARY ARE NOT REQUIRED, A STATISTICAL SUMMARY OF THIS _ INFORMATION MAY SUFFICE. Step 1 . Determine whether disposal of the subject waste Is limited to certain subtypes of the disposal practice under consideration. Consider the type and source of the waste stream and the legal and practical constraints on the subject disposal method. List the applicable subtypes and proceed to Step 2. Step 2 . If applicable, determine the proportional distribution of the subject waste between on-site and off-site facilities. This Information will be useful In determining which Individual sites are likely to handle the waste (Step 3). Consider the following In the absence of Information to the contrary. • Resldentlal/commerclal waste. If the waste derives from consumer use, assume that It Is disposed of off-site with MSW unless It Is discharged through the sewer system to POTWs. • Industrial waste. If the waste derives from Industrial operations, determine what percentage Is disposed of with MSW, what percentage Is disposed of off-site by private waste disposal businesses, and what percentage Is disposed of on-site. Take Into account whether the waste Is a hazardous waste, and use available Information on waste disposal practices. No generic data In support of this decision are currently available for nonhazardous Industrial waste. • Wastewater. By definition, all domestic wastewaters routed to POTWs are disposed of off-site. The percentage of Industrial wastewaters discharged Indirectly (off-site) will have been determined In Stage III. Step 3 . Identify the Individual facilities using the subject disposal practice that are probable candidates for disposal of the subject waste stream, based on Information derived from Steps 1 and 2 and available Inventories of facilities. The output of this step for a detailed exposure assessment will be a list of the sites and their locations. An estimate of the total number of facilities In the population may suffice for nationwide or regional exposure assessments that do not require site-specific modeling of environmental releases. 52 Step 4 . Ascertain whether Information exists on the capacity and current operating characteristics for the sites listed In Step 3. Use this Information along with available Information on the disposal practices of the source of the subject waste to estimate the amount of the waste stream disposed of at each facility. The output of Stage IV for exposure assessments requiring site-specific estimates of environmental releases will be a list of candidate sites and the quantity of the subject waste stream disposed of at each site. For exposure assessments that do not require site-specific modeling, the output may be as simple as the number of facilities and the average quantity of the waste handled per facility, or as complex as a statistical distribution of the population of facilities by waste quantity handled. 2.3.5 Stage V Decision Tree - Estimating Environmental Releases from Disposal Sites A flow chart showing the Stage V procedures Is presented In Figure 7. This stage Involves estimating releases to the environment from disposal, given the Stage IV estimates of the amount of waste handled at each disposal facility. For maximum accuracy In exposure assessments. Stage V release estimates should be made for each disposal facility. In nationwide exposure assessments, however, It may be Impractical to model releases from each site. This would be the case, for example, where exposure from a substance disposed of In all municipal landfills Is being Investigated. In these assessments, releases can be estimated from model environments representing the range of "typical" disposal facilities and extrapolated In a statistically acceptable fashion to a national scale. See Volume 1 of this series for a discussion of this and other planning Issues. Obviously, the Information compiled In Stage II on the physical/ chemical characteristics of the waste will be essential In this stage because releases are partially determined by characteristics of the waste containing the subject chemical. The following general decision tree Is a guide to the format of the decision trees for each disposal/ treatment practice. (Stage V decision trees tailored to landfills, land treatment, surface Impoundments, POTWs, Incinerators, and Injection wells are presented In Sections 3 through 8.) Step 1 . a. Identify the Important design and operating characteristics of the waste disposal method that affect releases to the environment. 53 54 ’IF SITE SPECIFIC ESTIMATES OF ENVIRONMENTAL RELEASES ARE NOT REQUIREO, A STATISTICAL SUMMARY OF RELEASES MAY SUFFICE b. Ascertain which of the parameters listed In l.a are known for the slte(s) of Interest based on accessible computerized data or other In-house Information. c. Identify which of the parameters listed In l.a but not l.b can probably be obtained from existing files at regional EPA offlce(s) and/or state solid waste agencies. Step 2 . a. Identify the available approaches for predicting environmental releases based on design/operating characteristics. If no approaches are available, then releases cannot be estimated. Otherwise, choose the appropriate approach and go to 2.b. b. Determine what site-specific design/operating characteristics are required for Input to the predictive approach chosen In 2.a. Decide whether these are readily available (see l.b). If not, determine whether there are "surrogate" values that can be used In place of the site-specific parameters. If there are no suitable Input data available, two options exist: (1) collect data listed In l.c or collect new data; (2) abandon the predictive effort. If Input data are available, go to 3. Step 3 . Using the chosen predictive method and Input data, estimate releases of the subject chemical from each disposal site receiving the subject waste. Alternatively, estimate releases from one or more representative sites (actual or hypothetical) and extrapolate these releases to a regional or national scale (see Volume 1 of this series). Consider using the Inventory compiled In Stage IV as a basis for this extrapolation. The output of this step should Include estimates not only of ultimate releases to environmental media, but also subject chemical mass/concentration In any residues that may result from the treatment/disposal practice. (Such residues Include Incinerator ash and POTW sludge). Step 4 . If monitoring data are available, compare with values estimated In Step 3. If estimated releases and chemical quantities In residues (If any) do not correlate with measured values, use best judgment to evaluate the discrepancy. If applicable, calibrate the model and rerun. Information on the subject chemical In treatment residues should be used as Input to Stage III for an analysis of ultimate releases from the residue. Then use the estimated releases as Input In the analysis of environmental fate and pathways of the final exposure assessment (see Volumes 1, 2, and 5 of this report). 55 3. LANDFILLS This section discusses the Information needed to estimate the potential for environmental releases of chemicals from landfills, and focuses on municipal. Industrial, and hazardous waste landfills. Landfills are of particular Interest because they are a major collective repository of wastes and have the potential to release toxic chemicals to air and water. General background material about landfill types and operation Is given In Section 3.1. Decision trees based on this Information are presented for Stage IV In Section 3.2, and for Stage V In Section 3.3. There are major gaps In the state-of-the-art knowledge on the behavior of chemical substances In landfilled wastes, which may seriously limit the ability to estimate releases from landfills. On the other hand, there Is a considerable body of knowledge on the types and amounts of wastes that are landfilled, as well as on landfill sizes, capacities, and operating characteristics, which will be useful In exposure assessments. 3.1 Background Information This section presents some Information on landfills that will be useful In conducting both site-specific and large-scale exposure assessments. Included for discussion are (1) the difficulties caused by having only very general Information on some types of landfills, (2) the current state of the art In estimating environmental releases from landfills, and (3) methods for estimating some site-specific Input parameters likely to be useful In modeling these releases. Some modeling-related considerations and Ideas on using the available Information In large-scale assessments are also discussed. 3.1.1 Landfill Types and Operation There are five types of landfills: • Municipal landfills . These primarily handle municipal waste and may be privately or publicly owned and operated. Municipal landfills may also accept other types of waste, such as nonhazardous Industrial, construction, and agricultural waste. There are an estimated 12,000 to 15,000 active municipal landfills In the U.S. (Petersen 1983, USEPA 1980f). • Industrial landfills . About 23 percent of all Industrial plants landfill on-site; there are presently about 76,000 on-site Industrial landfills (USEPA 1980f). Industrial nonhazardous waste disposed of off-site may also be handled at a municipal site. Since most off-site landfills handle a variety of waste types, no distinction will be drawn In this report between municipal and Industrial (nonhazardous) off-site landfills. 56 • Hazardous waste landfills . These differ from Industrial nonhazardous landfills by having to meet more stringent permitting, design, and operational criteria. There are about 500 on-site and 44 off-site hazardous waste landfills In the U.S. (Table 21 In Section 3.1.5; Table D-7 In Appendix D). t Construction landfills . Most constructlon/demolItlon waste Is disposed of In municipal landfills. Only a few landfills specialize In construction waste. • Agricultural landfills . Agricultural waste not returned to the soil Is usually taken to municipal landfills. No Information Is available on strictly agricultural landfills. Construction and agricultural landfills will not be considered further In this report because they are not expected to be major repositories for toxic substances subject to regulation (except for asbestos from construction wastes); moreover, very little Information Is available on these sites. The three most common operational practices for landfills are the area, ramp, and trench methods (Anon. 1981b). In the area method, wastes are spread onto the existing ground surface, compacted, and covered with earth from another source. This method Is useful with depressions that are to be filled as a landfill, or In building earthen structures above the surface of the existing ground. The ramp (or progressive slope) method Is a variation of the area method. Here the earth cover Is excavated from the ground Immediately In front of the active working face. In the trench method, a trench Is excavated and wastes are placed In the trench, compacted, and covered with soil. The excavated earth can either be used to cover the solid wastes In an adjacent trench or stockpiled to cover the wastes In the trench being excavated. The volume of waste covered with earth during each day's operation Is referred to as a cell or lift. The trench method Is the most common method used and Is required by some state regulations. Current use of the area and ramp methods Is not common. Calculations In this report will be based on the assumption that all landfills use the trench method. 3.1.2 Environmental Releases from Landfills (1) Leachate . Pollutant leachate Is generated when water enters the landfill, migrates through It, and picks up soluble materials from the disposed waste, either original waste compounds or the soluble products of biological and chemical degradation. Water can enter a landfill as precipitation, surface runoff, or Infiltration of groundwater (Patel et al. 1979). 57 Generation of leachate does not necessarily begin with the first addition of water. Solid wastes act like a sponge and are capable of storing about 135 to 270 8,/m 3 of material (1 to 2 gal/ft 3 ) (Anon. 1981b). Leachate will be generated only after this storage capacity (field capacity) Is reached and more water Is added. (In practice, channels may form within the waste which allow the water to flow through more quickly.) The time required for leachate generation Is highly variable and depends on local In situ conditions and rainfall (Anon. 1981a). Pollutant leachate may reach both groundwater and surface water, and many examples of leachate pollution have resulted In the contamination of water supplies or the habitats of aquatic life (CEQ 1981). The composition of leachate Is variable, because It Is highly waste- and site-specific. The chemical complexity of municipal solid waste (MSW) leachate Is Illustrated In Table 15. Leachate from hazardous waste Is even more waste-specific; no general figures can be compiled In a meaningful manner. Leachate may react chemically with landfill lining materials. Depending on the nature and concentration of constituents In the leachate and the nature of the lining materials, leachate may damage or cause failure of the liner. (2) Gases and dusts . Some of the decomposition products resulting from the microbial degradation of solid waste are In gaseous form. Although such degradation produces a variety of gases, methane and carbon dioxide are the major gaseous products of landfill decomposition. Migration of gas produced In a landfill may lead to a number of environmental effects, ranging from odor problems to the accumulation and explosion of methane (Patel et al. 1979). Theoretically, about 0.2 m 3 of methane gas can be produced from each pound of waste (Anon. 1981b). In addition to gaseous decomposition products, organic compounds In landfilled wastes may volatilize and migrate from the soil to the atmosphere. The continuous emission of these organic compounds. If they Include toxic materials, may cause significant harm to public health and the environment. Volatilization Is a function of temperature, wind speed, surface area, depth of burled waste, and waste characteristics. Because the volatilization and degradation processes may be slow, the emission of hazardous volatile organic compounds may persist for many years. Gas generation rates at landfills have not been well studied, and the extent of air contamination from these sites Is largely unknown (Shen 1981). Landfills that are poorly designed and operated may also emit dusts containing chemical substances. 58 Characteristics of MSW Leachates Reported In Five Studies -O 0 in o O O ov CN o • • • vo CN in § • r* Ov in • • • in 0 in in CN CN co • o • • • m • • r- *3- m • • • ^ i_ Ov vo vO m Ov in CN • • • — • r- o in • CN • • • • Li_ * * % •k * r- *3- CN CN Ov CN CN — © • o • • • o o o o • in O _ o • CN in VO CN r- ^3- cr • o • • • • o p o • o — vO • VO CN ^r in 00 n- c • o • • • r- r- CO • CN *3- • A • 1 • l CN m 1 • 0 i » •k a 1 A o CN — 1 A m o cr m — — 1 CN CN I CN — 1 i • a 1 Ov — O *3- CN o O o vO o rn —- O O —— o o o m • • • in CN vo o —— o •k V V — CD vO VO CN — O O — in ov • • CN — O — ir\ • — vo ov VO *-N o o O o • o O o ^3 o o in in VO O in • O 8 O O _ o o o o • • o O o • o o • CN • in CN • m m \ [ | 0 o o o n* • vO o o o O 00 o m — CN —— • m in vo 1 CD E H CJ C •k o CN at , « 3 ’ o 1 CN «k Ov •k * 3 - •k in •k A o A 1 in 1 in A A 0 M 0 T — o • A •k i i o VO r- Ov in O c cr T 1 in o o o vO CN CN N- •— o O o O o o o o O o O CO in Ov in in o o «k 0 * •k VO m 3 VO o _ — 0 > < • o • • o in • • o • • O • o • • • O • 0 O in © • o • • o • • • in • • O • o • • • • 0 O m M cr. • o • • in 00 • • CN • • Kf • • • • — • 00 in — M c 0 ___ A I o ■k in «k CN •k 1 in «k m 1 in J. cr in A CN • * 3 - l o O A A CN o O O O o CN CN © cr o o vO in vO in rH c CN 00 • • o O • o O Ov O o O 0 0 O vo 0 0 vO in CN vo ^ 3 - 00 • in O • 00 O • O • o 0 in rx O CN 0 cr % * «k «k 1 • oo OO • o 00 Ov in in vO — rx r*x 00 0 * 3 - Ov CN CN 1 r* •k «k «k «k A •k i •k A •k «k «k •k in CO N" 1 • o o ^ 3 - CN in o in — rx ~ i Ov A A vO O m CN CN in 1 * 3 - l CN i I VO 1 00 1 0 1 A O o ro • in • • o • O CN vO m o o in in 0 O TD TD CJ o • • •— •—» 0 in — —— in o — O Q 1 ^"X 0 0 in in o E in 4 — 3 O >- 0 TD TD TD \ 4 - E O) c ^-x 0 0 c c o •— in — 2 : CL zr ^ 3 - > TD © O JZ C in TD TD 0 O 'w' '— x_^ <^x O — c 8> o E •— © C O CJ 3 0 0 CO o 0 3 — c 0 CJ E 0 E z 4 - in CL L. — 0 TD 0 © £ 3 in 4 - 3 x-^ c c in in 4 - 0 u in E E TD lx. •— © 0 0 M 0 •— 3 •— u £• — 0 — 3 3 •— l_ w in c in E 4 - x^ c TD in c •— 0 -C 0 •— •— L. R © 0 CL in 3 0 o l_ •— u E U o c TD c cn in 0 U Q. — — — 4 - > — »— TD M —>■ Q. o 0 cn c O 4 - TD — c in 0 0 0 O •— 0 0 p 0 0 O L. 0 0 0 n O O 3 •— Q o 8 4 - 4 - 4 - © 4 - 4“ 4 - 0 O o o o — _l 2 : 2 CL CL CO c 0 8 ) m 1- o o — 0 N >x 0 c 0 0 c TD TD in 0 TD 3 0 in 0 .c in i- 0 > TD 3 4- in in 59 Source: USEPA 1983b. 3.1.3 Predicting Environmental Releases Much of what Is discussed In this section about groundwater models Is equally applicable to surface Impoundments (Section 5), modeling releases from land treatment (Section 4), and deep well Injection (Section 8). To avoid repetition, only salient points will be further discussed In Sections 4, 5, and 8. All models discussed In this section are Included In Appendix A. The reader Is also advised to see the companion volume on assessing exposures from drinking water (Volume 5 of this methods development series), since It contains a more detailed discussion of groundwater modeling. Environmental releases from waste disposal sites may be predicted by the use of models. In general, the models are composed of concise mathematical expressions that use a series of equations to express relationships among various physical and chemical parameters In the waste disposal system. Depending on the method of analysis and the accuracy required, these models may range In structure from a few simple algebraic equations solved manually to hundreds of complex differential expressions which must be solved through the use of computers. An Important consideration when deciding whether to use models Is the level of data needed. Often the amount of Information required by the model will exceed that which Is available for site-specific assessments. In this case, a great deal of time and money may be required to allow for accurate model output. Although the development and use of models for hazardous waste predictions have only recently received much attention, there are many models available to the Investigator. A recent report (Weston 1978) provides a compilation of the different types of models available for possible use In groundwater evaluation studies. The U.S. EPA Office of Solid Waste (OSW) (USEPA 1982a) reviewed approximately 400 models and selected those which may be of most use for their risk analysis requirements; some of these are mentioned below. However, even those selected by OSW have limited capabilities; because of the numerous factors affecting chemical fate at disposal sites, no single model Is capable of accounting for all variables. For this reason, most models do not attempt to predict all aspects of a chemical's fate; they are usually more specific In their objective. Some general classifications for which several models are available to choose from for particular modeling scenarios are: watershed simulation models, release rate models, and solute transport models, which are further divided Into unsaturated zone and saturated zone models. 60 The watershed simulation models have to be operated after each storm event to produce long-term simulations. Despite this, the results of long-term simulations tend to be more accurate than those for short-term simulations. An example of a useful model In this category Is PRZM (Pesticide Root Zone Model, developed by the EPA Office of Research and Development), designed to model the transport of pesticides applied to soils. Unfortunately, It does not take Into account the complexities Involved In modeling landfills (1.e., the relation between landfill structure, liners, and pollutant transport), and thus It Is of limited use. Release rate models permit estimation of the quality and quantity of leachate released from a site. Output from the release rate model Is used as Input for one of the solute transport models. There are at least six release rate models documented In the literature (USEPA 1982a); several others are under development by various researchers. One of these models, called HELP (Hydrologic Evaluation of Landfill Performance) (Perrier and Gibson 1980), was developed specifically to evaluate hazardous waste landfills. The program was developed by the U.S. Army Corps of Engineers, Waterways Experiment Station, and allows rapid estimation of the amounts of runoff, subsurface drainage, and leachate that can be expected from different landfill designs and local climatic conditions. The program requires site-specific clImatologlc, soil, and landfill design data (Including specifications for multi-layer and lined systems); default values can be assigned If these data are not available (except design data). Another potentially useful release rate model Is one developed for the rapid assessment of groundwater contamination under emergency response conditions (Donlglan et al. 1983). This approach makes use of easily-applied nomographs that are based on a transport- convection equation and requires Input data similar to that needed for other models. This model accounts for contaminant transport as well as release, so that It Includes features of some of the transport models described below. Additional models Include Release Rate Computations, Post-Closure Liability Trust Fund (PCLTF), and DRAINMOD/DRAINriL . More Information on these models can be found In Volume 5 of this methods development series. Solute transport models predict the dispersion of contaminants from the source. As mentioned above, they are capable of predicting chemical fate either In the unsaturated zone or In the saturated zone; the numerous hydrogeological differences between the two zones prevent them from being modeled together. Of the numerous transport models that have been developed, many are only for specific applications; however, several are more general In application and have been documented (USEPA 1982a) and field-verified. Most of these models solve a transport-convection equation In one, two, or three dimensions by a variety of methods (e.g., finite element methods, finite differences methods, or "random walk" methods). Three of the more familiar models currently In use are SESOIL, 61 the Seasonal Soil Compartment Model (Bonazountas and Wagner 1981), AT123D, developed at Oak Ridge National Laboratory (Yeh 1981), and the Random Walk Solute Transport Model, developed by the Illinois State Water Survey (Prlckett et a 1.1981). Other models are described In another reference (USEPA 1982a). SESOIL Is of particular use because It Is designed to be "user-friendly" and Is contained within the EPA Office of Toxic Substances' Graphical Exposure Modeling System (GEMS). GEMS Is a computer system that Integrates environmental modeling functions to aid environmental analysts In performing exposure assessments. SESOIL Is not currently tailored to estimating releases from landfills, however. Volume 5 of this series provides a practical model application Involving SESOIL and AT123D. Models also exist for estimating air emission alone (Hwang 1982, Shen 1981). Input parameters Include soil porosity, moisture content, bulk density, cover thickness, molecular weight of the subject chemical, temperature, and landfill area. 3.1.4 Model Input Data Depending on the type(s) of model(s) chosen to simulate the actual conditions at the site, the numbers and types of data required will vary. A brief discussion of parameters required for release rate and transport models Is presented below, followed by recommended procedures for obtaining some of the most common Input data. Release rate models are generally divided Into three necessary components, which respectively address leachate generation, constituent concentrations, and leachate release rates from the site. Definition of the primary factors affecting these components requires data such as precipitation characteristics (amount, duration, and frequency), water table elevation, evapotransplration rate, solar radiation, temperature, humidity, soil profile, hydraulic conductivity, and pressure head. Measurements or design characteristics of the landfill are also required. Transport models which rely on some method of solving a series of transport-convection equations require several physical and chemical parameters as Input. These Include void ratio, porosity, moisture content, hydraulic conductivity, dispersion-coefficients, Infiltration, depth to groundwater, hydraulic gradient, aquifer thickness, boundary conditions (e.g., areal extent of aquifer, presence of recharge boundaries), and chemical characteristics of the contaminant (e.g., adsorption coefficients). Recommended procedures for obtaining climatic, soil, chemical, and selected application-related geometric and application-specific data are presented below. 62 (1) Climatic data . For statistically related climatic Input, parameters are compiled manually from climatological data sheets of the National Weather Service office of the National Oceanic and Atmospheric Administration (NOAA). NOAA reports provide dally, monthly, and annual summaries of climatological data for designated sites throughout the U.S. Input parameters can also be compiled with the aid of a user-supplied computer program, using the climatological data from NOAA which Is recorded on magnetic tape. (2) Soil data . Required soil parameters can be derived from soil maps and Information prepared by the Soil Conservation Service (SCS), U.S. Department of Agriculture. Information Is available on the soil types of many (but not all) areas of the U.S., Identifying characteristics of the soil profile to a depth of 1.5 m (five feet). The SCS also prepares soil survey Interpretation sheets by soil series; these tabulate significant soil engineering properties, Including classification, permeability, water capacity, and pH for each major soil horizon. They also provide depth to water table and to bedrock (If less than 1.5 m), hydrologic group, suitability for various purposes, and nature and degree of limitation for certain uses Including sewage lagoons and sanitary landfills. Some models have the capability of assigning default values In the event site-specific data cannot be found, e.g., for typical soil categories and their associated parameters. These data can be used as surrogate data when releases are being calculated for a broad geographical area or when site-specific data are unavailable. Table 16 provides some examples of the surrogate soil data compiled for the SESOIL model. (3) Chemical data . Basic chemical parameters for the contaminants of Interest can be obtained from standard reference manuals and/or estimation techniques. (4) Application-related geometric and application-specific data . These data comprise a set of waste application-related geometric parameters (e.g., area of disposal site, depth to groundwater), and numerous application-specific parameters (e.g., pollutant loading, soil moisture). These data are sometimes available through the applicable state solid waste agency, at least for permitted sites. However, the printed Inventories of disposal sites distributed by most states (see Section 2.3.3) rarely contain this Information; It must be obtained through a personal visit to the state agency and a manual search of their files. An exception Is California, which has a computerized data retrieval system (see Appendix B). The following discussion proposes methods for obtaining generic data for non-site-specific applications; It will also propose methods for 63 Table 16. Precompiled Soil Parameters, SESOIL Data File Parameters So 11 type Soli density Intr1 nsIc permeabl1Ity Pore connectivity Index Porosity % OrganIc carbon (g/cnr 5 ) (cm 2 ) (-) (-) (?) Clay 1.32 1.0 x 10" 10 12.0 0.45 1.46 Clay-loam 1.32 2.8 x 10 -10 10.0 0.35 1.32 S1Ity-loam 1.32 1.2 x 10~ 9 6.0 0.35 3.00 Sandy-loam 1.32 2.5 x 10 -9 4.0 0.25 0.50 Source: Bonazountas et al. 1981. 64 estimating average parameters for broad geographic regions. The actual numerical estimates made here may be refined or replaced as the user becomes familiar with the methodology and as new sources of data become avallable. Assumptions and estimates are based on Information obtained from three EPA publications (USEPA 1979b, 1980b, 1980f) as well as from the periodic updates of the Waste Age Survey (WAS). The survey has been conducted on a more or less annual basis since 1974 by the editors of Waste Age , a trade journal of the solid waste disposal Industry. The survey contains Information on number, size, and classification of municipal landfills as well as other variables. Unfortunately, the recent surveys have been less comprehensive than the ones for previous years. The 1983 survey gives only the number of landfills, the number of sites with liners or monitoring wells, and the type of site ownership (see Table 17). It also Includes some of the results of the 1981 and 1982 surveys for comparison. The 1981 survey, although comprehensive In scope, was Incomplete, with fewer than half the states supplying data for some of the most Important data categories. Selected useful data from the 1981 WAS appears In Table E-2 In Appendix E. Each of the application-related parameters developed In this method Is discussed below; useful landfill size and capacity estimates are summarized In Table 18. (a) Depth to groundwater. Depth to groundwater Is one of the Important Input parameters that Is not readily available on a site- specific basis, except by a manual search of the facility files of the applicable state agency. Moreover, groundwater depth shows extreme variation from one region to another and cannot be calculated from other types of data. The groundwater depth parameter affects soil-moisture distribution In the soil column and, consequently, pollutant fate (transport and transformation). An approach for estimating groundwater elevations when site-specific data are not available Is given below. The U.S. Geological Survey (USGS) maintains a number of computerized data bases that contain water table levels on a site-specific basis, based on latitude/longitude. One data base, the Ground Water Site Inventory (GWSI), contains data from all 50 States and U.S. Territories. The quality and quantity of data, however, vary markedly from state to state. In addition to the nationwide data base, at least fourteen other similar data bases contain data on one or more states (see Appendix F, Table F-l, for a summary of these data bases). It Is recommended that the USGS state geologist or USGS district groundwater expert be contacted when these data are required In the course of exposure analyses. A current list of USGS state geologists Is given In Table F-2, Appendix F. 65 Table 17. Selected Data from the 1983 W aste Age Survey No. of landfills in state No. of open dumps No. to be up¬ graded No. of permits for new sites No. of sites with artificial liners No.of sites with monitoring wells Alabama 135 12 11 2 0 110 Alaska NA* NA NA NA NA NA Arizona 116 28 27 3 0 7 Arkansas 311 78 NA 12 0 0 California 542 40 31 6 0 NA Colorado 206 32 26 NA NA NA Connecticut 151 36 24 0 0 38 Delaware 35 4 4 0 1 6 Florida 248 55 17 15 8 192 Georgia 284 6 4 48 0 45 Hawaii 25 9 4 2 NA NA Idaho 132 42 20 11 0 8 Illinois 329 42 0 43 1 186 Indiana 348 191 2 14 0 44 Iowa 94 0 0 5 1 56 Kansas 224 1 0 27 0 NA Kentucky 128 34 NA 17 0 7 Louisiana 532 532 95 NA NA NA Maine 308 45 NA NA 2 28 Maryland 47 0 0 2 1 47 Massachusetts 283 81 NA 2 NA NA Michigan 362 150 0 20 4 53 Minnesota 185 60 0 2 0 NA Mississippi 253 133 10 19 0 4 Missouri 128 2 1 6 0 45 Montana 222 16 13 5 0 17 Nebraska 400 1 0 3 0 15 Nevada 99 52 10 4 0 4 New Hampshire 101 26 0 0 2 1 New Jersey 185 5 1 NA NA NA New Mexico 231 0 0 NA NA NA New York 525 56 38 NA NA NA North Carolina 167 1 0 7 1 0 North Dakota 130 0 NA NA 0 0 Ohio 318 54 NA 6 NA 50 Oklahoma 225 66 60 40 0 0 Oregon 226 28 3 11 1 16 Pennsylvania 925 94 75 3 15 190 66 Table 17. (continued) No. of landfills in state No. of open dumps No. to be up¬ graded No. of permits for new sites No. of sites artificial 1iners No.of si monitor well” Rhode Island 18 4 1 0 0 14 South Carolina 225 0 0 4 0 55 South Dakota 200 140 5 8 0 12 Tennessee 161 6 2 12 0 53 Texas 1075 11 8 26 0 58 Utah 296 26 8 6 0 1 Vermont 92 4 0 6 NA NA Virginia 209 50 34 52 0 47 Washington 136 36 18 NA NA NA West Virginia 127 41 36 NA NA NA Wisconsin 1085 66 10 7 0 195 Wyoming 0 0 0 38 0 5 Totals 12,991 2396 598 494 37 1609 *NA means data not available. Source: Petersen 1983. 67 Table 18. Landfill Size and Capacity Estimates 3 Parameter Metric 6 Enqlish Industrial solid waste density 1,000 kg/m 3 (62.4 lb/cu ft) Municipal solid waste densityc 593 kg/m 3 (37 lb/cu ft) Landfill capacity (volume) 30,228 m 3 /ha (43,000 cu ft/acre) Landfill capacity (mass) Industrial waste 29,900 Wkkg/ha (13,334 tons/acre) Municipal wastec 17,850 Wkkg/ha (7,963 tons/acre) Per capita waste generationd Rural >1 kg/day (>2 lb/day) Urban <4.5 kg/day (<10 lb/day) U.S. average 2.3 kg/day (5 lb/day) Average trench depth 10 m (30 ft) a Based on data and assumptions discussed in Section 3.1.4(4). See Table 19 for estimates specific to landfilling of municipal sludges, bwkkg - wet metric tons. c Based on average in-place density of co-disposed municipal and industrial wastes. d()n the basis of a 365-day year. 68 Unless a site listed In these data bases Is located close to the disposal facility of Interest, It Is advisable to compile the computerized water table data from several sites In the area of Interest, using latitude/longitude or any other geographic Information, such as county name. Determine the average groundwater depth. Sometimes the computerized data bases do not provide data for the geographic area of Interest; sometime the precise locations of disposal sites will not be known. Several alternative approaches are possible In these cases. One approach Is to base assumptions on the known pattern of wetland and floodplain distribution (see Figure F-l In Appendix F); one can at least determine whether the water table In a given region Is relatively high or low, and select an arbitrary value or set of limiting values on that basis. Alternatively, water table levels typical of unllned surface Impoundments In the area could be used (see Section 5.3). Another general source of Information on groundwater Is a publication by US6S (USDI 1963), but It does not always provide water table Information for a given region. When the locations of disposal sites are not known, one approach Is to estimate the distribution of landfill sites based on population distributions for the subject area. Landfill acreage Is not distributed evenly throughout a region, but Is concentrated In areas of high population density. This Is certainly true of municipal landfills, and to a lesser extent of Industrial landfills, despite the Increasing tendency for Industry to develop In rural areas. After the relative proportions of landfill acreage In wet and dry zones Is calculated, limiting values may be selected to represent the likely range of groundwater depths for each zone. Table E-l In Appendix E provides estimates of population distribution with respect to wetlands. (b) Depth of unsaturated soil zones. Depending on the model used, one or many separate unsaturated soil layers may be modeled. Landfill layers, covers, and liners may therefore constitute separate "soil" layers for the purposes of modeling. Simulations of landfills with Impermeable clay liners or coarse solid wastes are possible with some of the models now available. The following are default estimates of depths of various discrete layers In landfills that may be useful In modeling: • Average depth of fill material: 10 m (USEPA 1980f) • Average depth of single cell: 2.5 m (USEPA 1980f) • Depth of dally cover: 0.2 m; depth of final earth cover: 0.6 m (as prescribed by most state regulations). (c) Pollutant loading. Pollutant quantities originating from the site may be Input to the model In several ways, depending on the model 69 selected. If the pollutant Is assumed to be present as a concentrated mass, as In a landfill, a leaching rate from the waste must be specified. If the pollutant Is already mixed Into the soil, as In some landspreading operations, the total pollutant concentration present In the upper soil layer can be given. Usually, It will not be possible to determine the leaching rate directly. Although a number of studies estimate leaching rates of various chemicals In soil (Rouller 1977, Wlgh and Brunner 1979, Streng 1977, O'Donnell et al. 1977), few. If any, data are available on leaching rates of pollutants In the waste mass Itself, which Is highly chemical-specific. Until the state-of-the-art understanding of this process Is more refined, leaching rates from the waste mass will have to be determined on a case-by-case basis. Unavailability of this Information constitutes a major data gap. (d) Area to be modeled. Assuming that the subject waste Is disposed of throughout the year, the area to be modeled will be equivalent to the area of the landfill that Is utilized annually. Landfill capacity and rate of fill Information Is rarely available except by manual search of state files. Estimates must be derived from whatever data are available on the basis of the assumptions discussed below. Estimates for landfill area are presumed to apply equally to municipal and Industrial off-site landfills. The 1981 Waste Age Survey (Anon. 1981c, see Table E-2 In Appendix E) divides landfills Into six size categories according to capacity expressed In tons per day (tpd). Most (76 percent) fall Into the smallest size category (0-50 tpd, or 0-45 metric tons per day). It can be assumed that these serve smaller populations In the rural areas, while larger facilities serve more urbanized regions. Some rural areas undoubtedly have Initiated regional systems, In which case the solid wastes from these areas would be disposed of In a large capacity landfill; however, for calculation purposes, It will be assumed that rural landfills uniformly accept a maximum of 45 metric tons per day of waste each. The area of an urban landfill can be estimated by consulting the Waste Age Survey for the relative size distributions of larger landfills within the subject state (see Table E-2 In Appendix E). In general, the total regional municipal landfill area should be proportional to the regional population distribution. All on-site Industrial (hazardous and nonhazardous) landfills may be assumed to fall Into the smallest size category (0-45 metric tpd) (USEPA 1980f) . 70 The above assumptions permit an estimate of the probable capacity of a given landfill; however, they do not directly satisfy the modeling Input requirement of "area to be modeled." To achieve this, one must have an estimate of the waste capacity per unit landfill volume. In general, four Interrelated factors Influence the amount of waste that can be disposed of per hectare. These are (USEPA 1980b): • The overall size of the landfill. This defines how much area can be used for disposal and how much area must be used as buffer around the disposal area. The smaller the landfill, the greater the proportion of acreage which must be used as a buffer. • The size of the trenches. A typical trench may have surface dimensions of 30 by 60 m and have an average depth of 10 m. • The percentage utilization within a trench. The percentage of trench utilized for waste disposal depends on the materials being disposed of and the spacing practices of the operator. • The density of the material. There Is significant variability depending on the actual wastes being disposed of, discussed In detail below. Industrial (hazardous and nonhazardous) waste Is usually a liquid or sludge or a relatively dense, homogeneous solid. Therefore Its density will be assumed to approximate the density of water, 1,000 kg/m 3 (62.4 lb/cu ft. or 8.34 lb/gal), a commonly accepted assumption In the disposal Industry (USEPA 1980b). Municipal waste Is considerably less dense; even after compaction and mixing with co-dlsposed Industrial waste, the average density of total mixed waste accepted by municipal landfills Is estimated at 593 kg/m 3 (37 lb/cu ft) (USEPA 1979b). The average capacity per acre of landfill Is assumed to be 30,228 m 3 /ha (16,000 cu yd/acre); this estimate has been confirmed by Industry representatives (USEPA 1980b). On this basis, 29,900 wet kkg/ha, of Industrial waste occupies one hectare, and 17,850 wet kkg of municipal waste occupies one hectare. See Table 19 for capacity estimates pertaining specifically to landfilling of municipal sludges. Therefore, In the absence of site-specific Information, the following equations can be used to determine the area of a given landfill utilized for waste disposal In one year. Note that the formula for Industrial waste assumes that such waste Is generated continuously. If the subject waste results from a batch manufacturing process, the necessary adjustments should be made to reflect the smaller volume occupied by the waste. 71 Table 19. Recommended Design Criteria for Disposal of Municipal Sludge in Landfills 1 1 & V4- Cl X) 3 c 35 r— • r* 4-> O’ to 05 L. 0 U 05 L. &. CL 4-> TO O M 0 c 0 V4- >p> -*—> r— l/> s r— 05 • r— CL o c .Q JD 4-> 05 1 TO CM 05 4-> 0 4-> ■S £ 4-> C c •*-> 00 00 L. CO C 05 05 c C 05 o E o r— £3 0 3 u Q. oo u 4-> t o 0 § L. Q. U U 4-> TO O 0 o TO Cl u o (1) L_ 3 c r— 05 •k s Q O’ *o 3 >> r— CL a • r* 0 0 o r— 05 Q N i- iO c on 0 OsJ • * *o ,r— cd 05 O • cd o 4-> 0 r— 4-> •r* O TO 4-> O c l/> • r* oo 3 4-> 0 05 10 0 3 05 O — 8 E JD 05 > 00 U 4— > 00 o 4-> 0 u o CM 1/5 —J o O «k CD 05 r— x: •r- 0 \ O CO co_ ** 00 TO E L. in 3 0 r— 4-> f— 8 > u oo 05 c TO 05 o r— 05 C TO CL 4-» n *o 3 0 U P— r— 4-> 0 o U r- ro r— r— N u l_ CL • r— u • r— CD 0 O o *4- 0 r— v*- 4-> r— 4-> 4-> •r> r— 0 05 05 -O 0 L. ID O o 05 0 05 > Q. oo CM 4-> o L. L. +-> 0 0 • o < C5 CO —J >- O 05 £3 TO r— N 0 — 0 CO U O CD E g V4- 05 00 TO TO •r— Ql 3 O C CM 0 00 r- o 35 c U 4-> 00 CD Q C o Q. L. 05 • r" 05 •*-> sD £3 T5 4-> >> CL U CM t— 4-> 0 05 r— 05 N 4-> JO CM CL O . r— u • r> • r— 05 4-> w»- 0 r— E 4-> o *— 4-> tr- • r— 4-> o 05 05 iO 3 o o 05 0 03 00 Mi 1/0 4-> o U U 4-> o 0 • • < C5 CO z >- o vO 0 to 4-> 4-> u r— 05 C •r> • r— U 0 4-> o u 4-> U) oo c 0 c • r" O 4-> o t- TO 4- • r- u 0 0 O 4-> P 4-> U 05 l/> o 00 O O u TO 05 0 3 • r- 05 * p* !_ & S' 4-> 0 Q- r— 05 05 CD CL o jC r— u l- "O s 00 U Mi 3 05 05 CD r- 0 0 TO C C 10 0 o> CD C • r- . r— CD ■o X5 3 o TO 3 3 O r— »— 4-> 3 r— S- 3 3 r— CO CO C5 CO CO l/> cd o CO CD < O- LU co 0 u L_ 3 O CO 72 For landfills accepting only Industrial wastes: kkq/dav x 260 (dav/vr l* = hectares filled annually (3-1) 29,900 kkg/ha For landfills accepting municipal or mixed munlclpal/lndustrlal waste: kkq/day x 260 (dav/vr )* = hectares filled annually (3-2) 17,850 kkg/ha Occasionally, the exact amount of waste received by a given facility may be reported In state-supplied Inventory data. A few states (e.g., Texas) provide data on the size of the population served by each municipal facility. Using per capita waste generation estimates for the subject population, one can convert "population served" Into "kkg/day of waste generated," equivalent In this case to the amount of waste received by the facility. Per capita waste generation ranges from about 1 kg/day for rural populations to about 4.5 kg/day for urban populations. The nationwide average Is 2.3 kg per capita per day (City of Ann Arbor 1981; NEMCOG 1980). These numbers can be used In the following equation (note that municipal waste generation Is computed on the basis of a complete 365-day year): dally per capita waste generation x 365 x population served (3-3) 17,850 kkg/ha = hectares filled annually Capacity data may also be expressed In terms of acre-feet (one acre-foot Is equivalent to 1,220 m 3 ). This can be converted Into area by assuming that average trench depth Is 10 m. EPA's Hazardous Waste Data Management System (HWDMS) provides capacity data In this form for each hazardous waste landfill (see Section 2.3.3(4), Exhibit D-l, and Table D-4 In Appendix D.). However, this figure represents the total proposed area of the facility, which Is not necessarily equivalent to *Represents the average number of landfill operating days per year. 73 actual area. The reason Is that permit applicants often claim for their facility a larger area than they Intend to use Immediately, In order to allow for future expansion. Assuming that the proposed area Is Indeed equivalent to operating area, the area filled per year can be calculated on the basis of a presumed ten-year lifespan for the average landfill (USEPA 1979b). These calculations have a low confidence level because of the many assumptions Involved. An alternative method for estimating off-site hazardous landfill areas Is to consult Table 20. The total off-site hazardous landfill area utilized annually In the subject EPA Region can be divided by the number of hazardous landfills In that Region (see Table 21) to obtain an estimate of the average area utilized In a single landfill. Despite the wide variation In Individual landfill sizes, this method Is probably more accurate than the preceding one, since Table 20 Is based on actual amounts of hazardous waste landfilled In one year and thus fewer assumptions are Involved. 3.1.5 Additional Considerations for Modeling Chemical Releases from Landfills There are several parameters that may not be specifically considered as Input data which must be taken Into account when landfills are modeled. For large-scale exposure assessments where many landfills must be considered, the number of landfills containing the chemlcal(s) of Interest must be known. In addition, the presence of a liner or leachate collection system, the extent of waste preprocessing, and several other factors should be known. Each of these factors Is discussed below. (1) Number of facilities . The total number of sanitary landfills and open dumps In operation In 1983 Is given In Table 17 for each state. The exact number of municipal landfills currently In operation Is not known. In 1976, the Waste Age Survey reported 15,821 sites; In 1977, 14,126 landfills were counted. There are two conflicting estimates for 1978, both based on estimated updates of the 1977 survey; these are 18,307 (USEPA 1979b) and 14,689 (USEPA 1980f). Sources of error and uncertainty Include the Inadequacy of state-supplied data and the Increasing rate of landfill closings. Future trends are difficult to predict because of the changing regulatory climate. Industrial on-site landfills (hazardous plus nonhazardous) are estimated by state In Table 22 and by Standard Industrial Classification (SIC) code In Table 23. 74 Table 20. Off-Site Hazardous Landfill Area Utilized Annually EPA Region Estimated total waste disposed of, thousand wet kkq Total landfill area 3 , hectares Number of landfills Area per landfi11. ha 1 6 0.2 1 0.2 2 375 12.5 2 6.3 3 170 5.7 3 1.9 4 226 7.6 2 3.8 5 330 11.0 11 1.0 6 650 21.7 10 2.2 7 62 2.1 3 0.7 8 unknown - none b - 9 822 27.5 10 2.8 10 59 2.0 2 1.0 a Derived on basis of assumptions explained in text (Section 3.1.4(4)(d)). Assumed that typical landfill capacity is 29,900 wet kkg per hectare. b No permitted sites; the number of landfills improperly receiving hazardous waste is unknown. Source: USEPA 1980b and Versar estimates. 75 Table 21. Cannercial Off-Site Hazardous Waste Disposal Facilities C O an > CD -O l<- +■> 4-> O on O 0) ro CO X CD S CD O) — <4- ro on O -*-» a c • r— C/> S *8 “D L) l- l/> C L. ro CD CO CD M U on CL. ro •r- D -C > O U JZ (D -t-> in c O) -r- c .r- on “D r— CD CD r— >f U- r- •r- 4-» o *o 14- *r- C *D -*-> +-> ro c c C jC (O ro 3 _J Z5 Q CD cr E ■*-> CD *-» < on c ro • r- 2 L. CD o»- i+- O __ ro -O 4-> TJ O (D 4-» r— TD 14- C O ro -C CD CD CD rO 4-> 4-> on C ro CD S U u on CD 13 Q_ s i- ro rsi «o -C *0 a; “o -*-> Q) !/> -a i c ro (/> v+- CD O — 4-» l_ .f- 0 •— E O 3 rO C7 in O ^ O O M O f\j OI r-* r-» (\J CO if) lO C\J if) ro — c\j co to 00 — c\j co n -- o ro o o (\j m vO 8 CD cd i£> C\J < H- o *— rsjro^j‘tr>vr>r^cDcy»o i/i CD T3 ro c x: ro 4-> C to o • f- • r— a) 4-» 0) c CD ,r ” -*-> “D on 0) -♦-> S ro u i/i a> — c (D _ O) U rO rO in -C ro “O 4-> C C CD CD u u i- L. CD CD 0 l Q_ ro JD CD cd < a. LU in Z) CD u u u o in 76 Table 22. Industrial On-Site Landfills by State 3 State Number of landfIlls Alabama 1, 150 A la ska 74 Ar Izona 469 Arkansas 652 CalIfornla 8,648 Colorado 638 ConnectIcut 1,580 Delaware 125 Florida 2,218 Georqla 1,694 Hawa1 I 151 Idaho 275 II11nols 4,580 1nd1 ana 1,890 Iowa 805 Ka nsas 691 Kentucky 723 Loulsi ana 84 5 Ma 1 ne 432 Maryland 757 Massachusetts 2,497 MlchIgan 4,412 Minnesota 1,372 Mlsslsslppl 608 Missouri 1,514 Montana 201 Nebraska 382 Nevada 91 New Hampshire 313 New Jersey 3,625 New Mexico 21 1 New York 7,693 North Caro 11 na 1,985 North Dakota 104 Ohio 4,488 Oklahoma 756 Oregon 1,093 Pennsy1 van la 4,368 Rhode Island 660 South Carol 1na 871 South Dakota 1 16 Tennessee 1,236 Texas 3,480 Utah 300 Vermont 190 Virginia 1,029 Wash 1ngton 1,221 West Virginia 41 1 Wlscons 1n 1 ,998 Wyoming 84 TOTAL 75,705 including hazardous waste landfills. Source: USEPA 1979b. 77 Table 23. Estimated Number of Industrial Landfills By Size Category f u. C — O — O TO C L. © ( 1 ) — -Q 6 3 © >* © to V cr 4 GO — o o o nt o O o nt o o o in nt vO o O _ o o in 1 «— «-• nt CN in in VO o N- vO vO 00 o r- nt o o 00 vO ON O in vO _ O 00 VO 00 vO nt CN CN o VO —— r^ in o 00 i in nt o nt in — in nt in ON In nt in o ■k •k •k % •k % «k •k % «k «k «k •k % VO — in CN — nt —— vO 00 — — nt in CN in 4“ c cn © c — — © c L — 4- © — — in I TO C C O 'o ~ Vi oooooooooooooooooo o o CNCNCNCNCNCNCNOOOOinCNOCNOO CN CN CN CN CN CN CN CN CM CN (\| h- CN CN CN CN CN CN o i/> O CO & 4- •—» c 1 o © in o © —— CN 4- CL O) A ^ O (0 c m * o — +- TO © — © L. >. — JO © © o E C ■o in 3 2 © cn NT vO CN co I O' ^ cn ^ in I i— I i NT O VO CN VO h tJ- in Q 4- in Q_ c © 7 1- © •• O O 4— CL in in cn I © c o * o CN — CO r^ m 8 ON r^ vO 00 m 00 o s o NT r- o •am w CN o nt nt nt vO ■~ vO ON ON CN in r- vO 00 00 4- © TO — CN CN ON CN o O rn O ON r- CN VO ON L. © — ■k ■k % •k •k «k •k * •k •k «k ». •k •k •k «k © L_ >* CO nt ON vO CN — CN ON m in VO ON o CN 00 in in • • JO © © O CN CN m Mi —- CN N- —— — _J E C TO in < 3 2 8) *^> »- O in 4— V u cn 3 —- c in TO *4- — t O 4- — c l_ c 4- 3 3 CL © © C 4- to C E © O t o cn TO — >- CL — © L_ c © in JZ L- o *4- • 3 CL — ■M o u © 3 in 3 in to — — in C CT C c O ■§ in M 4— «— — © TO © 0 cn L_ — © in © c E 4- c CL — —— © in 4- M a c © — in J0 TO — © © © O in in V in — ti —» 3 C CL © E E 4- 3 > in © CL © 4- 4- © C o L_ i_ © — 3 TO © © TO L_ — © c © © 4- 4- o E TO © TO « in E C — E © 4— © 4- _o E c © in o © O L_ C —— 3 © u 4— O U L. 3 © E 3 b. O M L. 3 © © © i- >- © © — O in l_ —■ "a O —— © CL 4- — o L. © •k L. O L. CL in 4- Mi in c O —• — L. 4- — 0 © j= © 2 — *© 4- in © m © © — TO 5 $ © TO C 8. C § L JO 4- c E l- 1 O c c u 4- O CL O L_ — JO © O — JO c © © o —- in O o o © CL o 3 © L_ -C © 3 © 4- L. © o — L_ t. — c li_ »- h- < Li_ CL Q_ O CI¬ QC _l to Q_ L_ 2 LU h- Q_ © TO © cn CJ TO O o CN m in vO r^* 00 ON O M CN m ^r in vO 00 ON to O CN CN CN CN CN (N CN CN CN CN m m m NO m m m m NT NT © o 00 ON < & 53 © U L. 3 <2 78 Almost all Industrial on-site landfills fall within the 0-50 tpd (0-45 kkg/day) size category (Table 23). These are filled at the approximate rate of one-half hectare per year (based on Equation 3-1). The total on-site landfill area filled each year by each SIC group Is shown In Table 24; these estimates were obtained by applying the conversion factor from Table 18 to Industrial waste generation data from USEPA 1979b. The approximate area of municipal landfills used annually Is estimated In Table 25 based upon the same assumptions applied to other published data (USEPA 1977). (2) Liners . A few models currently take Into account the effect of natural or synthetic liners on pollutant migration. Others do not; this may represent an Important gap In the ability to predict emissions from landfills, depending on the particular model chosen. Ideally, the bottoms of all landfills should be lined with an Imper¬ meable membranous lining; the proposed regulations of many states and current federal regulations make this mandatory for new sites. Existing landfills may or may not be lined. In actual practice, the 1983 Waste Age Survey (Peterson 1983) reported that only 37 out of nearly 13,000 municipal landfills In the U.S. currently operate with liners. In the absence of specific Information for each site, age Is perhaps the best Indicator as to whether a liner Is present. When considering regional data. It Is reasonable to assume that older nonhazardous and municipal sites (ca. 10 years) are not lined. In the case of a specific site that Is known to be lined, an assumption will have to be made as to the rate of leakage or tearing. The Information resources Investigated In this study provided no tools with which to estimate the leakage rate. The effects of leachate on liner permeability are currently under study (Haxo 1976, 1979, 1980; USEPA 1983b). Since hazardous waste disposal sites must meet more stringent operating and design criteria, many of them are lined. Consult the regulations of the subject state; these may prescribe layers of earth compacted to given specifications In lieu of synthetic or natural clay liners. (3) Leachate collection . RCRA hazardous waste regulations require all new sites and existing sites that will be expanded to have some kind of leachate collection system. This would affect release estimates, reducing groundwater contamination to zero (at least theoretically) and adding steps to the methodology, since collected leachate must Itself be disposed of In some way. Leachate disposal options Include various treatment methods, landspreading, and recirculation to active portions of the fill. At the present time, however, only 26 out of approximately 12,000 municipal facilities are known to collect leachate (Anon. 1981c). It Is extremely unlikely that leachate Is being collected at on-site nonhazardous Industrial landfills. 79 Table 24. Industrial On-Site Landfill 3 Acreage Used Annually SIC Code Total kkg/yr disposed Industry (xlO^) Total TPY° disposed (xIO 6 ) Hectares Acres 22 Textile-mill products 3.7 4. 1 126 315 23 Apparel 12.7 14.0 431 1,077 24 Wood products 17.7 19.5 600 1,500 25 F urn 1ture 4.8 5.3 163 408 26 Paper and allied products 3.2 3.5 108 269 28 Chemicals and allied products 11.8 12.9 397 992 29 Petroleum 0.91 1.0 31 77 30 Rubber, plastics 0 0 0 0 31 Leather 0.36 0.4 12 31 32 Stone, clay 8.5 9.3 286 715 33 PrImary metal s 3.5 3.8 1 17 292 34 Fabricated metals 15.7 17.3 532 1,331 35 Nonelectrical machinery 67.5 74.2 2,283 5,708 36 Electrical machinery 0 0 0 0 37 Transportation equipment 5.3 5.8 178 446 38 Professional and scientific Instruments 3. 1 3.4 105 262 39 Mi seellaneous manufacturing 7.9 8.7 268 669 includes hazardous waste landfills. b TPY = tons per year. Source: Conversion factor from Table 18 applied to industrial waste generation data from USEPA 1979b. 80 Table 25. Municipal Landfill Acreage Used Annually EPA Reqion Number of landfills Acres Hectare I 1,122 190 76 II 936 1,340 536 III 930 1,130 452 IV 1,611 1,930 772 V 2,973 3,550 1,420 VI 2,706 3,240 1,296 VII 1,277 1,530 612 VIII 1,206 1,440 576 IX 890 1,070 428 X 1,038 1,250 500 a Based on estimated total of 14,689 landfills (USEPA 1980f). Source: Conversion factor for municipal landfill capacity (Table 18) applied to 140 million tons municipal waste generated annually in the U.S. (USEPA 1977) distributed regionally on the basis of landfill size distribution by state (Anon. 1981c, Waste Age Survey). 81 (4) Preprocessing . The preprocessing of waste by shredding and/or baling affects the production and composition of leachate and gas from the waste, and would also affect the leaching rates of chemicals from the waste. The nature and extent of these effects are still under Investigation (Hentrlch et al. 1979; Elfert and Swartzbaugh 1977). Currently, only 33 facilities reportedly mill, shred, or grind waste (Anon. 1981c). These procedures are not applicable to most Industrial waste. 3.1.6 Estimating Emissions from Broad Geographical Regions The exact method of estimating environmental releases from broad geographical regions will depend on the nature of the exposure assessment and the models used; however, a general approach Is outlined below. Data on the soil, climatic, and other conditions available In the region of Interest can be combined or averaged with the generic data compiled In this report. From these data, one or more hypothetical landfills embodying these parameters can be designed. An exposure assessment then can be conducted using the hypothetical landflll(s) as the source. Alternatively, sets of high and low values can be selected to represent the range of these variables, for which modeling of releases can then be performed. In designing hypothetical landfills, site-specific operational characteristics (e.g., capacity, depth of fill, density of waste accepted) can be assumed to average out to the figures given In Section 3.1.4(4). 3.1.7 Monitoring Estimates of chemical releases and concentrations can be checked against any available monitoring data. However, monitoring data are uncommon and are limited to few. If any, toxic chemicals. About 12 percent of all functioning landfills are known to have monitoring wells (Petersen 1983). Monitoring data at landfills may Include one or more of the following types: leachate, groundwater, soil particles, or waste composition. Monitoring data are also submitted to the applicable state agency and to EPA regional offices In quarterly reports. These are not available except by personal visit to the agency and a manual search of their files. Additional data have been derived from physical models representing scaled-down replicas of landfills (Elfert and Swartzbaugh 1977, Hentrlch et al. 1979, Streng 1977, Wlgh and Brunner 1979). Extrapolation of monitoring data from one site to another Is not advisable because of the many variables which affect releases of chemicals from a site, particularly site-specific physical, climatological, and operating conditions (Weston 1978). 82 3.2 Allocating Waste Streams to Landfill Sites - Stage IV Decision Tree Using available Information on the disposal practices used for various types of wastes and the design and operating characteristics of the different types of landfills, one can estimate the proportion of each Individual waste stream that Is likely to be disposed of at landfills In the study area. Because site-specific Information Is not readily available for most landfills, considerable Individual judgment Is needed. For site-specific estimates, the output of Stage IV will be the location of each landfill receiving the subject waste, and the quantity of subject waste received by each landfill. For calculations of environmental releases that apply to broad geographic areas where the locations of Individual sites are Irrelevant, only the estimates of total landfill population and of the amount of waste received by one or more representative model landfills are necessary. Consult Section 3.1 for suggestions on parameter values to use In nationwide or regional exposure assessments. For Stage IV determinations, consult the following sections: For municipal landfills . Section 3.2.1 For nonhazardous Industrial landfills . Section 3.2.2 For hazardous waste landfills . Section 3.2.3 3.2.1 Municipal Landfills Step 1 . Identify landfills that are probable candidates for disposal of the waste stream of Interest and locate them on a map of the study area. Some states have compiled Inventories of municipal landfills which list their locations (see Table B-l, Appendix B). For states not listed In Appendix B, contact the state solid waste agency. Table D-3, Appendix D, for this Information. Step 2 . Estimate the amount of the waste stream of Interest disposed of at each facility (In quantity/year). Consider the capacity and operating characteristics of each facility (If available) as well as the distance from the source of waste. The distribution of this waste stream among the candidate sites will depend on the nature of the waste. For example, If It Is a residential waste that Is generated uniformly by the 83 population, assume that Its distribution among landfills Is proportional to their relative capacities. If capacity Information Is not available, assume that the average rural landfill has a capacity of 0 to 45 kkg/day. Urban landfills are larger, and the Waste Age surveys (Table E-2, Appendix E) should be consulted to determine the most prevalent capacity range In the states Included In the study area. Alternatively, If population data are available for the area served by each landfill, Equation 3-3 can be used to estimate landfill capacity (see Section 3.1.4(4)(d)). Step 3 . If no Information Is available for Step 2, assume that all of the waste stream of Interest Is disposed of within a few miles of Its point of origin. The cost of hauling generally makes long-distance transportation of waste economically unfeasible. Allocate an amount of waste to each landfill on this basis, and produce a list of landfills In the study area that Indicates the estimated amount of waste handled at each site. Then, use average climatological and geological data for estimating releases In Stage V. 3.2.2 Industrial Nonhazardous Landfills Step 1 . Determine the percentage of the waste stream of Interest that will be disposed of on-site versus off-site. This Information will be a useful tool In Step 2. References already consulted for Stage III may have provided this Information. If no Information Is available, proceed with Steps 2 and 3 below; then deduce the probable proportion of on- and off-site facilities based on the estimated numbers and capacities of each (see Stage III). Assume that all waste generated by facilities known to have on-site landfills Is disposed of on-site. Step 2 . Identify the landfills that are probable candidates for disposal of waste stream of Interest. To locate off-site facilities, • Determine whether the subject state supplies facility Inventories. (Table D-3 lists phone numbers of applicable state agencies.) Consult these for locations; note whether any distinction Is drawn between municipal and off-site Industrial landfills. Otherwise use the nationwide Waste Age Surveys (see Tables 17 and 22) to get at least a rough Idea of the number of potential Industrial landfills In the state(s) of Interest. 84 • Note that nonhazardous waste Is often disposed of with hazardous waste to avoid the expense of separating waste streams. If this Is likely to be the case with the waste stream of Interest, conduct a HWDMS retrieval (Section 2.3.3(4) and Exhibit 0-1 In Appendix 0.)). Step 3 . Estimate the amount of the waste stream of Interest disposed of at each facility. The output of this step should be a list of facilities and the estimated annual amounts of the waste received by each facility. Consider the capacity and operating characteristics of each site (If available) as well as the distance from the source of waste. The cost of hauling generally makes long-distance transportation of waste economically unfeasible. Therefore, the waste Is probably disposed of at the nearest facility of sufficient capacity to accept It. If the exact location of the facility cannot be determined, assume that the waste Is disposed of within a few miles of Its source of origin. Then, use average climatological and geological data for the county for calculations of Stage V releases. 3.2.3 Hazardous Waste Landfills Step 1 . Determine the percentage of the waste stream of Interest that will be disposed of on-site versus off-site. References already consulted for Stage III (Section 2.3.3(4)) may have provided this Information. If no Information Is available, proceed with Steps 2 and 3 below; then estimate the probable proportion of on- and off-site facilities based on the estimated numbers and capacities of each (see Stage III). Assume that facilities with on-site capacity will treat and dispose of the waste on-site, provided that their facilities can handle the waste. Step 2 . Identify the landfills that are probable candidates for the disposal of the waste stream of Interest. a. Conduct a HWDMS retrieval to obtain facility locations (see Section 2.3.3(4) and Exhibit D-l In Appendix D). (This may already have been done In Stage 3.) Be sure to Include off-site commercial facilities In the retrieval. 85 b. Contact the subject state (see Table D-3) to verify and add to the list compiled In 2.a. Many states supply Inventories of hazardous waste disposal sites, often specifying the exact types of wastes treated. (Although HWDMS may also supply this Information, the data are considered unreliable.) One useful source of Information Is the State of Kansas, which supplies a list of all commercial hazardous waste handlers In the Midwest (see Exhibit B-2 In Appendix B). Step 3 . Estimate the amount of the waste stream of Interest disposed of at each facility (In quantity/year). The output of this step will be a list of facilities and the estimated annual amounts of the waste stream of Interest received by each. Consider the capacity and operating characteristics of each candidate facility (If known) as well as the distance from the source of the waste. For facilities that are known to have on-site landfills, assume that all of the waste Is disposed of there unless other on-site disposal methods are known to exist. Otherwise, the waste will probably go to the nearest commercial facility of sufficient capacity to accept It. Note that the capacity reported by HWDMS Is the proposed capacity, which may not be the same as current operating capacity. See Sections 3.1.4 and 3.1.5 for suggestions on using capacity data. Note that Information on types of waste accepted, If available (obtained In Step 2), may eliminate some sites from consideration. The amount of uncertainty In these estimates will vary depending on the assumptions used, but will generally be lower than for nonhazardous landfills. 3.3 Estimating Environmental Releases from Landfills - Stage V Decision Tree Environmental releases will normally be estimated using a mathematical model. In Stage V, the user evaluates available Information on design/operating features of the landfills In the study area. This Information, In conjunction with the Stage IV estimates of the amount of waste received by each facility. Is used as Input to the model to estimate releases of chemical substances to air and groundwater. Ideally, the output of Stage V will be the total annual quantity of the subject wastes emitted to air, groundwater, and surface water from each Individual landfill, or from statistically representative landfills In the case of broad regional estimates. For the steps required by Stage V for municipal landfills, see Section 3.3.1; for Industrial (hazardous and nonhazardous) landfills, see 3.3.2. 86 3.3.1 Municipal Landfills Step 1 . Select a model to estimate environmental releases of the waste of Interest. For nationwide or broad regional estimates, see Section 3.1.6. Estimated total municipal landfill area used annually Is summarized by EPA Region In Table 25. For site-specific determination, see Step 2. Step 2 . Assemble the data necessary to run the model. The following types of data will probably be required for most relevant models. • Climatological data • Soil data • Chemical data $ Geometric, application-specific data. Climatological and soil data will be assembled from the data sources detailed In Section 3.1.4. Chemical Information Is available from standard reference manuals. Geometric, application-specific operational information may be more difficult to obtain. Step 3 . Estimate other operational parameters as needed for model Input. a. Pollutant loading . Determine the proper format for the pollutant quantities at the site that have been estimated In Stage IV (Section 3.2) and compile these data. The manner In which these data are Input to the model will depend on a number of factors, especially on whether the waste mass Is consolidated or well-distributed. Consult Section 3.1.4(4)(c) for an explanation of the factors Involved. b. Depth to groundwater can be determined from statewide computerized data bases, If they are available for the subject states, or from one of the USGS data bases described In Section 3.1.4(a). In the absence of such data, a default value (or set of limiting values) can be selected on the basis of the Surface Impoundment Assessment (SIA) data base (see Section 5), soil maps, wetland distribution data for the subject state (see Section 3.1.4), or other general references. 87 c. Depth of various soil zones . Section 3.1.4(4)(b) provides default figures for depth of fill, earth cover, and similar data. Unless there Is Information to the contrary, assume that no liner or leachate collection system Is present. d. Landfill size (surface area) . Individual landfill capacity Is occasionally Included In state-supplied Inventory data. In the absence of site-specific data, assume that a rural landfill has a capacity of 0-45 kkg/day. Urban landfills are larger; consult the Waste Age Surveys (Tables E-2, Appendix E) to ascertain the most common capacity range for larger landfills within the subject state. To convert capacity Into landfill volume, use Equation 3-2 (Section 3.1 .4(4)(d)). Landfill area Is then calculated by dividing the volume by the landfill depth (If known; otherwise use an average depth of 10m.). This method should be reasonably accurate when the exact landfill capacity Is known. The amount of error Involved In these estimates depends on whether site-specific or generic data are used. Facility Inventories of some states provide data on populations served by each site. In this case, landfill area can be estimated by Equation 3-3 (Section 3.1 .4(4)(d)). Step 4 . Using the model of choice and the assembled Input data, estimate environmental releases to air and groundwater for each landfill receiving the waste stream of Interest. Output should Include the following: • Flux of the subject chemical entering the groundwater after a given period of time. • Flux of the subject chemical volatilizing from the soil Into the atmosphere after a given period of time. • Concentration of subject chemical remaining In each designated soil zone after a given period of time. Step 5 . If monitoring data are available (which Is highly unlikely), compare them with the predicted concentrations of the chemical of Interest. 88 Comparison of monitoring data with release estimates requires considerable expertise, because there are many variables that complicate the comparison, Including problems related to lab analysis and temporal and spatial variation In pollutant concentration. If estimated concentrations do not correlate with measured values, use best judgment to evaluate the discrepancy. Estimated releases may be used as Input In the analysis of environmental fate and pathways and In the final exposure assessment, discussed In Volume 2 (for ambient exposure) and Volume 5 (for drinking water exposures). 3.3.2 Industrial Landfills (Hazardous and Nonhazardous) Estimation procedures for environmental releases are similar to those for municipal landfills, with some additions. Step 1 . See Step 1 of Section 3.3.1. The total on-site Industrial landfill area used annually Is summarized by SIC code In Table 24. Off-site landfill disposal of Industrial nonhazardous wastes may be presumed to occur at municipal sites, except In states that supply separate data for Industrial and municipal sites. Step 2 . See Step 2 of Section 3.3.1. Step 3 . a. See Step 3.a of Section 3.3.1. Also, note the following: In the case of manufacturing wastes. It Is Important to know whether the wastes are generated during a batch or continuous process. (This Information may have been compiled for the ambient exposure scenario.) This will determine whether the subject pollutant will be concentrated In a few Individual cells or spread more or less evenly through the landfill. b. See Step 3.b of Section 3.3.1. c. See Step 3.c of Section 3.3.1. Also, note that the presence of liners and leachate collection systems will have to be taken Into account. d. See step 3.d of Section 3.3.1. Also, for hazardous waste sites, the HWDMS provides data on the proposed facility capacity. Care should be taken In using these data, however, as this does not necessarily represent actual operating capacity. Note that Equations 3-1 and 3-3 assume that the subject waste Is being generated continuously. In cases where the waste results from a batch manufacturing process, the necessary adjustments 89 should be made to reflect the smaller volume occupied by the waste. ( A similar adjustment will be necessary when pollutant loading Is estimated; see Step 3.a above). When the subject pollutant Is disposed of only a few days a year, note that the average depth of a single cell, representing one day's accumulation of waste received. Is about 3 meters. Step 4 . See Step 4 of Section 3.3.1. Step 5 . See Step 5 of Section 3.3.1. 90 4. LAND TREATMENT This section presents methods for evaluating exposure to chemical substances from land treatment. There Is sometimes little site-specific Information on land treatment, with the exception of hazardous waste land treatment sites and some municipal waste sites. Therefore, the kinds of data available will be more suited to nationwide large-scale exposure assessments than to more detailed assessments, unless site-specific Information Is collected. Some generic data to support such assessments were developed In this methods development effort. The background material on which the methods are based Is given In Section 4.1, followed by the Stage IV and Stage V decision trees In Sections 4.2 and 4.3, respectively. 4.1 Background Information Soil Is a natural environment for the deactivation and degradation of many waste materials through physical, chemical, and microbiological processes. Land treatment Is a disposal technique by which liquid wastes or sludges are mixed with the surface soil to promote these processes, particularly microbial decomposition of the organic fraction. If the land treatment site Is managed properly, the treatment processes described below can be carried out repeatedly on the surface of a disposal site. In practice, sludges or wastewaters are either hauled or piped directly from the treatment plant or from an Interim storage or evaporation lagoon to the disposal site. The sludges are applied to the land by spraying, spreading, or subsurface Injection. The field may then be disked or plowed by conventional farm cultivation equipment. Nutrients or other soil amendments may be added to Increase biological activity, and the soll/waste mass may be mixed periodically to maintain aerobic conditions. The process of land treatment appears to work In a wide range of climatic conditions; however, warm, humid climates offer the most favorable conditions since biodegradation of the organic fraction Is enhanced with adequate moisture and high temperatures. Land cultivation has been used In cold and dry climates, but the waste degradation rates under such conditions are relatively slow. Many sites are located In relatively wet areas, occasionally within a few meters of the water table (so that pooling may occur). These are examples of poor site selection; besides Increasing contamination potential, excessively wet conditions hinder proper mixing of soil and waste. Landspreading promotes the aerobic decomposition of organic waste. This reduces Its volume, prevents the formation of unwanted gases, and minimizes the Intensity of leachate problems. The site may be returned 91 to almost any other land use, often Including agriculture. Active land treatment sites are often used for growing crops. Possible disadvantages of this method Include the need for relatively large tracts of land, long-term release of waste to the atmosphere and groundwater, Impact on vegetation grown on the site, and uptake of chemical substances by food-chain crops (Ross and Phung 1978). The EPA Office of Solid Waste (OSW) has recently published a technical resource document on hazardous waste land treatment which Is the most comprehensive and up-to-date source available on land treatment In general (USEPA 1983a). That document Includes a survey of hazardous waste land treatment sites as well as general Information on recommended practices. Other sources Include a state-of-the-art study sponsored by the EPA's Municipal Environmental Research Laboratory (Phung et al. 1978), and various research reports (Berkowltz et al. 1980, Phung et al. 1977, and Ross and Phung 1978). Nationwide, 221 facilities have applied for Resource Conservation and Recovery Act (RCRA) permits for the land treatment of hazardous waste (Table D-7 In Appendix D), and a recent survey located 197 operating facilities (USEPA 1983a). 4.1.1 Types of Waste Treated Several types of wastes are treated by landspreading. This Includes wastewaters and sludges from Publicly Owned Treatment Works (POTWs), wastewaters and sludges from private Industries (Including some hazardous wastes), and municipal solid waste. Current land treatment practices for each of these wastes are discussed below; estimates of the volumes of waste landspread by a few Industries are provided In Table 26. (1) POTW wastewaters . POTW effluents are sometimes landspread (usually after secondary treatment). About 600 communities In the U.S. use this practice, which Is most prevalent In arid or semi-arid areas (Culp 1979). There are three basic approaches to land treatment of liquid POTW effluent: Irrigation, overland flow, and Infiltration-percolation. In the Irrigation method, wastewater Is applied to land by fixed or moving sprinklers or by surface spreading. In the overland flow system, wastewater Is sprayed over the upper edges of sloping terraces and flows down the hill through grass and vegetation; the runoff wastewater Is diverted Into collection channels. The Infiltration-percolation method Is primarily a groundwater recharge system whereby wastewater (after secondary treatment) Is put Into spreading basins so that It can percolate Into the ground. This method does not attempt to recycle nutrients through crops. 92 Table 26. Landspreading Activity, Dry Weight Activitv Current volume kkq/yr Textiles 5 Petroleum 50 Pulp and Paper Negligible Leather 24 Food Processing - dairy products - breweries - wineries - canned and frozen foods - feedlots 120 3 217 400 62,000 Municipal wastewater treatment - to food chain land - nonfood chain land - giveaway/sale 750 250 500 Total except feedlots 2,319 TOTAL 64,319 Note: The estimates in this table were taken directly from the source, thus do not reflect more recent data provided in Table 6 (Section 2.3.3 (2) and in the recent OSW survey of hazardous waste land treatment sites (USEPA 1983a). Source: USEPA 1979b. 93 (2) POTW sludge . Nationwide about 24 percent of the POTW sludge generated Is applied to land, one half of which Is landspread on food chain land (see Table 6 In Section 2.3.3(2)). Several cities apply liquid sludge to cropland. Larger cities may pump the sludge through pipelines to the disposal site. The city of Chicago ships POTW sludge by barge to strip-mined land 200 miles away to restore the land to agricultural uses. In most cases, however, sludge Is transported by tank truck. Economic considerations usually prohibit the hauling of sludge more than a few miles from the point of origin (Phung et al. 1978). Sludge may be dewatered and dried and applied to land as a soil conditioner. The city of Denver plows dry sludge cake Into the ground at a nearby disposal site. Nationwide, approximately 18 percent of the POTW sludge Is distributed for marketing (Table 6 In Section 2.3.3(2)). For example, Houston sells Its dried sludge to a contractor In Florida to fertilize a citrus grove. Milwaukee markets bagged heat-dried POTW sludge through large distributors In all 50 States and some foreign countries. It Is presently Impossible to track the ultimate Individual disposal sites of wastes distributed In this manner. (3) Industrial wastewaters . Some land treatment of wastewaters has been practiced by the food processing, pulp and paper, textile, tannery, wood preserving, and pharmaceutical Industries. At most locations, the practice Is primarily used for wastewater treatment, rather than for land reclamation, so that little or no effort has been made to Incorporate wastewater Into the soil (Ross and Phung 1978). Table E-5 In Appendix E provides a nationwide breakdown of the number of hazardous waste land treatment sites by Industry, based on a survey reported In USEPA 1983a. That survey did not differentiate between sites receiving Industrial wastewaters and sites receiving Industrial sludges. (4) Industrial sludges . Land-treated Industrial sludges are either organic (e.g., oil refinery, paper and pulp, and fermentation residues) or treated Inorganic wastes (e.g., steel mill sludge) containing low concentra- tlons of extractable heavy metals. When the sludge Is applied to agricultural land, It Is primarily for disposal. The sludge Is also used as soil amendment. Among Industrial sludges, oil refinery wastes are disposed of most extensively by this method. (Of the 197 hazardous waste land treatment sites Identified In the OSW-sponsored survey (USEPA 1983a), 101 received petroleum refinery wastes. Types of oily waste disposed of Include cleanings from crude oil, slop emulsion, separator bottoms, and drilling muds. The sludge Is applied to the land by spreading It to a depth of about 7 to 20 cm and disking It Into the soil. Mixing Intervals vary from once per week over several weeks to twice per year. The practice Is 94 strictly for disposal; no crops or vegetation other than weeds grow at the sites (Ross and Phung 1978). Disposal Is usually on-site. See Table E-5 In Appendix E for a listing by Industry of the number of hazardous waste sites. As stated above, this table does not distinguish between Industrial sludges and Industrial wastewaters. An Increasing number of off-site commercial operators are treating wastes, especially hydrocarbons, by landspreading. Some hazardous waste Is landspread at commercial facilities, often after treatment In solar evaporation ponds. Table 27 shows (by EPA Regions) quantities of waste treated In off-site commercial facilities. It has been estimated that only about 3 percent of all Industrial sludge and wastewater Is suitable for disposal by land treatment (Ross and Phung 1978). (5) Landspreadlng of municipal solid refuse . Although this practice Is uncommon at the present time, a program for landspreadlng shredded municipal refuse has been Instituted by the City of Odessa, Texas. About one fourth of Odessa's refuse Is currently being disposed of In this manner; the goal of the project Is to landspread 90 percent of the city's refuse. The primary purpose of the undertaking Is for land reclamation. So far, 130 ha (50 acres) of the 610-ha (1,500 acres) site Is being so utilized. Application rates are approximately 220 kkg tons per hectare (100 tons/acre). Whether other cities have similar programs Is unknown. No significant Increase In nationwide landspreadlng of municipal refuse Is expected (Phung et al. 1977., 1978). 4.1.2 Environmental Impacts and Environmental Releases There Is a growing body of Information on the extent of environmental contamination from land treatment of waste. It Is somewhat limited partly because Impacts are chronic rather than acute; pollutants may move slowly and take decades to leach through soil Into groundwater. The previously mentioned 0SW technical resource document (USEPA 1983a) Is the most comprehensive source available on the processes associated with environmental releases from land treatment sites. Wastes applied to surface soils are susceptible to surface runoff from precipitation, although some sites contain drainage control facilities. Flood problems are occasionally reported and are due to poor site selection (Phung et al. 1978). Groundwater quality may be Impaired If leachate penetrates to aquifers. Waste pretreatment can reduce the potential for this problem. The waste load applied to the soil can be regulated by pretreatment, process modification, or the addition of soil amendments (USEPA 1983a). Most organic compounds are eventually decomposed by soil microorganisms. 95 Table 27. Commercial Off-Site Hazardous Waste Disposal Facilities Offering Land Treatment/Solar Evaporation Services in 1980 a by EPA Region Amount of waste handled. Percentage of EPA Reqion Number of facilites thousands of wet metric tons Percentage of off-site wastes handled c total wastes handled d I 0 0 0 0 II 0 0 0 0 III 1 NA NA NA IV 1 _b _b _b V l e NA NA NA VI 3 117 b 11.4 b l.l b VII 0 0 0 0 VIII 0 0 0 0 IX 6 345 64.5 12.2 X 1 75 21.6 7.5 TOTAL 13 537 8.8 1.3 NA - Data not available a Includes both land treatment and solar evaporation because the two practices are often closely related. Evaporation ponds are often used for physical separation and dewatering, which is followed by application of the sludges to the land. b Data for Regions IV and VI were combined to protect confidential information. c Percentage of all off-site handled waste that is land-treated. Percentage of all hazardous waste generated in the Region that is land-treated off-site. Currently inactive (7/81) Source: USEPA 1980b, USEPA 1983a. 96 Unless the soil Is overloaded with toxic substances, land treatment Is not likely to pose a serious threat to groundwater quality (Ross and Phung 1978). Early detection of leakage through a properly designed and maintained monitoring system remains the best way to prevent serious contamination (USEPA 1983a). Environmental releases to the air may result from landspreading activities. Wastewaters and sludges may volatilize on exposure to the atmosphere, Impairing air quality In the disposal area. Volatilization may result In a release to the air, although much of the readily volatile fraction would have come off during waste handling prior to delivery to a disposal site. Subsurface Injection of the waste or mixing It with soil can alleviate these problems, but It may not eliminate them (Ross and Phung 1978). Probably the most significant potential human health hazard Is the uptake of chemical waste by food-chain vegetation. Long-term effects of land treatment on crop quality and the food chain are not known. Toxic metal accumulation In particular may pose a serious threat. If a soil Is burdened with more waste than It can absorb, It may become anaerobic, resulting In nuisance odors and failure of the system to degrade the organic matter effectively. Furthermore, unless the wastes are decomposed to nonharmful products, the soil zone receiving the wastes could eventually become overloaded. As a result, disposal activities at the site would have to be terminated, rendering the site unusable for alternative purposes for many years (Ross and Phung 1978; USEPA 1983a). 4.1.3 Location of Sites In a detailed exposure assessment. Individual sites should be located before releases are estimated. This Is not always possible, however, because of the lack of reliable Information on land treatment sites that receive other than hazardous wastes. On-site Industrial facilities by definition are located at the manufacturing plant. Hazardous waste land treatment facilities, both on-site and off-site can be Identified by a retrieval from the Hazardous Waste Data Management System (HWDMS) (see Section 2.3.3(4) and Exhibit D-l In Appendix D). The OSW survey of hazardous waste land treatment sites reported In USEPA 1983a, however, contains more Information on Individual sites than does the HWDMS data base. For each site In the U.S. the following data were collected: 97 • Name and address of facility § EPA ID number • Phone number and contact • Size (acres) • Type (by RCRA hazardous waste code) and amount of waste (tons/yr) • Industry description and SIC code • Additional available miscellaneous Information The user must consult USEPA 1983a for this site-specific Information, which was too voluminous to Include In this report. Summary data from the survey, however, are Included In Appendix E of this report. Figure E-l and Table E-4 summarize the geographic distribution of hazardous waste land treatment sites In the U.S. Table E-5 lists the location of all known sites by Industry (Including SIC code). Fields used for off-site landspreading of nonhazardous Industrial and POTW wastes may be disposal facilities as such, operated by municipalities or commercial commercial disposal firms, or they may be privately-owned farmland whose primary purpose Is crop production. In neither case are they likely to be listed In state-supplied facility Inventories. If the sites are not listed, It may be reasonable to assume that they are located close to the source of the waste, since long-distance transportation of wastewaters and sludge Is not economically feasible. Environmental release estimates can then be based on general climatological and soil data for the entire county. There Is currently no way to determine the ultimate disposal site of sludge that Is dewatered and distributed for marketing. 4.1.4 Estimating Environmental Releases The general discussion In Section 3.1.3 on modeling releases from land disposal sites Is applicable to land treatment sites. Models used to estimate releases from land treatment sites should take Into account the reduction In chemical concentrations over time due to biodegradation and chemical and photochemical degradation. Environmental releases from land treatment sites can be predicted by several models, Including the Pesticide Root Zone Model (PRZM) and SESOIL. A description of SESOIL Is Included here to Illustrate In general the Issues and procedures associated with modeling environmental releases from land treatment sites. An example of a practical application of SESOIL Is Included In the companion volume on assessing exposures from drinking water (Volume 5). SESOIL was developed by M. Bonazountas of A.D. Little, Inc., (ADL) of Cambridge Massachusetts and Is a mathematical model for long-term environmental pollutant fate simulations that describes water transport, pollutant transport/transformation, and soil quality. It may be used to 98 predict leachate contamination of groundwater as well as gas emissions to the atmosphere (Bonazountas and Wagner 1981). SESOIL has been applied to several waste disposal practices, Including Industrial landspreading (Bonazountas et al. 1981) and the disposal of burled solvent drums (Wagner and Bonazountas 1981). SESOIL Is designed to be used to estimate environmental releases on a site-specific basis as well as across broad regions or nationwide (using hypothetical or "average" environments). Model simulations are based on a three-cycle rationale, the water cycle, sediment cycle, and the pollutant cycle. The water cycle takes Into account rainfall, Infiltration, exfiltration, surface runoff, evapotransplratlon, groundwater runoff, snow melt, and Interception. The sediment cycle Includes sediment resuspension due to wind and sediment washload due to rain storms. The pollutant cycle characterizes convection, diffusion, volatilization, adsorption/desorption, chemical degradation, complexatlon of metals, biological actions, hydrolysis, oxidation, and nutrient cycles. The user has the option of running the model on one of four different levels of spatial and time variations. Typical outputs of SESOIL Include: • Temporal and spatial pollutant concentration distributions In soil-air, soil-moisture, and on soil particles of the soil compartment. • Leachate migration In the unsaturated zone. • Pollutant migration (releases) from the unsaturated soil zone to the air. Aside from predicting chemical distributions In the unsaturated zone, other SESOIL outputs Include hydrologic relationships among precipitation, surface runoff, Infiltration, evapotransplratlon, soil moisture and groundwater runoff. Concentrations are reported according to the level of application. An advantage In using SESOIL for modeling of the unsaturated zone Is that It can be used with Input and output data files that have been developed to support Its use. (Table 16 In Section 3 provides a subset of the SESOIL soil data file.) SESOIL can provide a detailed mechanism, with a high degree of accuracy, to model contaminants In the unsaturated zone with minimal effort. The results can also be used as Input Into a model designed for the saturated zone. 99 4.1 .5 Model Input Data Table E-3 In Appendix E lists all the Input data that may be required to run the SESOIL model. (Not all the parameters are required for most applications.) There are five classes of Input data: climatological, soil, chemical, application-related geometric, and application-specific. Soil , clImatoloqlcal , and chemical data can be obtained as described previously for landfills. The range of possible parameter values may be slightly narrower than for landfills, however, because the soil and climate must be conducive to biodegradation. Some Information related to these parameters Is provided below, followed by a discussion of Information related to selected geometric, application-specific characteristics. Land treatment sites are usually relatively flat, with slopes less than 1 to 5 percent. The soils at these sites vary over a wide range of texture and permeability. One site, for example, started operating In beach sands, although eventually the drilling muds being disposed of there significantly changed the texture of the surface soil (Phung et al. 1977). In general, land treatment sites should not be established on extremely deep, sandy soils because waste migration to groundwater may result. The best soils for land treatment Include; loam, silt loam, clay loam, sandy clay loam, silt clay, or sandy clay (USEPA 1983a). The nature and extent of on-site vegetation will affect the evapotranspl- ration rate and hence the environmental release rate. Land preparation generally entails scarification of the surface to expose as much soil area as practical. Vegetation Is usually removed, but the smaller bush and grass may be left In place to be mixed with the waste. Grasses In the disposal plot will become established If the plot Is left Idle for some time. Many sites are farmed extensively, being used for wheat, corn, or other crops. Active land treatment sites are frequently used for turf farming (Berkowltz et al. 1980). The range of possible climatological parameter values may be slightly narrower than for landfills, because warm, humid, climates offer the most favorable conditions for biodegradation, figure E-l In Appendix E shows that the land treatment sites are generally located In the south, southeast, and west. Among the required application-related geometric and application-specific parameters for modeling are several parameters that were Investigated or suggested for use In the methodology. These parameters Include the following: 100 • Depth to groundwater • Depth of various soil zones • Surface area of the site • Pollutant loading Estimation of the depth to groundwater and the depth of the soil zones was discussed In the section on landfills (Section 3.1.4 (4)). The discussion applies equally well to land treatment sites, with the following modification: the layer of waste Incorporation at land treatment sites usually will be considered the upper unsaturated soil layer for the purposes of modeling. The depth of this layer may range anywhere from a few centimeters to 60 centimeters. The surface area of land treatment sites Is not always available and must sometimes be estimated. The surface area of hazardous waste land treatment sites (In acres) was tabulated In the recent OSW survey (USEPA 1983a). Surface area Is also available In the HWDMS as "proposed capacity" (In hectares). Proposed capacity, however, Is not necessarily equivalent to the area actually used for waste treatment; area data from the HWDMS may be used as an upper limit. For Industrial facilities for which no Information on surface area Is available, a "typical" surface area might be estimated from the data In the OSW survey. Figure E-2 In Appendix E gives the size distribution of land treatment facilities In that survey. Although the facility sizes range from 0.005 (.002 ha) to 1668 acres (675 ha), the median size Is only 13.5 acres (5.5 ha), and the distribution Is skewed towards the small facilities. If necessary, the user can obtain a similar estimate for the Industry or region of Interest by examining the survey data for the sites of Interest (In USEPA 1983a). It seems reasonable to assume that land treatment sites treating nonhazardous Industrial waste will have similar surface area distributions as those sites treating hazardous wastes. Surface area for municipal wastewater treatment plants can be estimated based on the fact that they need an estimated 40 to 240 ha (100 to 600 acres) per mgd (million gallons per day) capacity (Culp 1979). The plant capacity Is available from the Needs Survey data base as discussed In Section 6 and Exhibit H-l and Table H-8 In Appendix H. In the absence of more reliable Information, the surface area of a land treatment site can be calculated as shown In Equation 4-1 In cases where the application rate, the quantity of waste applied per unit area, and the frequency of application are known or can be estimated. 5 = A (4-1) B x C 101 where S = surface area of site A = quantity of waste (mass per year) B = application rate (mass per surface area per application) C = frequency of application (times per year) There are difficulties in compiling data for Equation 4-1. Application rates may not be known, and there is Insufficient information at this time to estimate average application rates for many types of waste. Annual land treatment application rates (equivalent to B x C in Equation 4-1) identified in the literature reviewed in this study, not including the results of the OSW survey (USEPA 1983a), are given in Table 28. A better source of generic data might be the OSW survey (USEPA 1983a); typical annual waste application rates for the land treatment facilities considered representative of the wastes of Interest in an exposure assessment can be compiled from the survey data. The lowest economically feasible application rate is 10 kkg/ha/yr (USEPA 1979b); this may be taken as a lower limit in the absence of other data. It may also be difficult to supply a value for "quantity of waste." Application rates are sometimes expressed in terms of total liquid volume; to fit in Equation 4-1, the quantity of waste must be expressed in units compatible with the units used for the application rate. Ideally, total waste stream volume and chemical concentration will be supplied by Stage III estimates, from which the chemical loading (in terms of mass) can be calculated. To further complicate estimations, sludge quantity may be expressed as either wet or dry weight, making direct comparison impossible if the solids content is not known. The solids content of sludge as applied appears to average about 5 percent to 7 percent, but may be as high as 20 percent (Berkowitz et al. 1980, Phung et al. 1978, Ross and Phung 1978). Sludge that has previously been stored in an evaporation basin will have a higher solids content. The frequency of application is also highly variable, ranging from several times daily for municipal wastewater to once every few years for certain types of waste (USEPA 1983a). There appears to be no published information on which to base reliable estimates of this parameter, and the confidence level for any assumptions made is low. The model input parameters of surface area and pollutant loading are closely Interrelated. An accurate estimate of pollutant loading requires reliable information of the application methods used, in addition to accurate estimates of the waste application rate. Wastewaters are not usually plowed into the ground, but sludges may be plowed or Injected to a depth ranging from a few centimeters to 60 cm (Berkowitz et al. 1980). When wastes are Incorporated into the soil, the depth of incorporation may be taken as the upper soil zone for a model such as SES0IL, and the loading expressed as the pollutant concentration in that zone. If waste is applied without 102 Table 28. Annual Land Treatment Application Rates 3 Waste stream kkq/ha Leather manufacturing wastes 800 Mun icipal/industrlal wastewater treatment sludge 140-230 b Plastics manufacturing 50-70 Petroleum refining Oily wastes and drilling muds 9,500-15,000 API separator sludge 2,000 a Flgures based on one or a few observations; not a statistically representative sample. ^Reported application rates range as low as 1 kkg/ha (USEPA 1980g). Source: Berkowitz et al. 1980, Phung et al. 1978, Wetherold et al. 1981, Culp 1979. 103 Incorporation, the Infiltration rate Into the soil must be specified. This may not be known, and will be a significant data gap. The depth of waste Incorporation Into the soil will also be needed If pollutant loading Is to be estimated from monitoring data concentration In soil rather than from known waste application rates. In the case of multiple applications to the same surface within a year, the timing of the repeat applications must be known to estimate total environmental releases accurately. This Information can be obtained only by direct contact with the waste generator or disposal site manager. If It Is not available, It will be a significant data gap. 4.1.6 Monitoring Monitoring data for chemical substances released from land treatment sites are generally not available In readily accessible (1.e., computerized) form. There are a few published studies that assess environmental releases from land treatment, notably the previously mentioned technical resource document on hazardous waste land treatment (USEPA 1983a) and Wetherold et al. (1981). Hazardous waste land treatment sites have to be monitored under the RCRA technical land disposal regulations published In Interim final form In 1982 (USEPA 1982c); however, this monitoring data will be accessible only by manual retrieval from EPA Regional offices. Additional monitoring data may be available from applicable state agencies. 4.2 Allocating Waste Streams to Land Treatment Sites - Stage IV Decision Tree In this stage the user will attempt to enumerate the specific land treatment sites that will receive the waste and the amounts treated at each wasteslte. In practice this will be difficult for many land treatment sites because of the paucity of site-specific data. There are methods of estimating the amounts treated per site, however, In the absence of site-specific Information, which are presented In the decision tree. The first step In the decision tree Is to narrow down the possible land treatment sites to those that are likely candidates for the waste. This Is done by considering various waste categories separately. Then the quantity of waste tested Is estimated for each site using all available site-specific and generic Information. Step 1 . Identify and list the land treatment facilities that are probable candidates for disposal of the waste of Interest. a. Hazardous wastes . Examine the summary 1983a presented In Figure E-l and Tables E-4 this report to Identify land treatment sites of Interest that potentially treat the waste survey data from USEPA and E-5 In Appendix E of In the geographic area stream of Interest. Be 104 sure to examine the sites listed under SIC code 49 (for commercial waste disposal facilities) In addition to the sites listed under the Industrial SIC code of waste generator. Consult the site-specific survey data (Table 2 In Appendix A of USEPA 1983a) for additional Information on candidate sites. If any. This Information may be supplemented with a Hazardous Waste Data Management System (HWDMS) retrieval (see Section 2.3.3(4) and Exhibit D-l In Appendix D of this report). Printouts available at the EPA Office of Solid Waste (OSW) list all hazardous waste land treatment facilities within a given area and their capacities (arranged by zip code and waste facility Identification number). b. Nonhazardous Industrial waste . Contact the applicable state solid waste agency (see Table D-3 In Appendix D). Most states will supply Inventories of waste disposal sites (often Incomplete or limited to permitted sites). Unfortunately, few states regulate land spreading of nonhazardous materials, and such facilities are rarely Included In state Inventories. In addition, consider the possibility that the waste of Interest Is disposed of In an on-site hazardous waste land treatment facility Identified In Step l.a, above. If no Information Is available, proceed to Step 2.b. c. POTW wastewaters and sludges . It may not be possible to determine the location of off-site land treatment facilities for POTW sludge, since many such sites are privately owned farms using the sludge as fertilizer for crops. Even publicly or commercially owned and operated POTW sludge landspreading facilities may not be listed In state-supplied Inventory lists. Contacting POTWs that are known to land treat wastewaters and sludges (from the Needs Survey data base, see Sections 2.3.3(3) and 6, and Exhibit H-l In Appendix H) may provide Information on the locations of Individual sites. If no Information Is available, see Step 2.b. Step 2 . Estimate the amount of waste disposed of at each facility (In mass or volume per year). a. References already consulted for Stage III may have provided Information on the percentage of the waste stream that Is disposed of on- and off-site. For on-site Industrial land treatment facilities (for hazardous or nonhazardous waste) Identified In Steps l.a or l.b above, assume that the total quantity of waste generated on-site Is disposed of on-site. 105 In cases where the Industrial waste Is likely to be disposed of at commercial land treatment facilities Identified In Steps l.a or l.b, assume that the total quantity of waste generated by a given source Is disposed of at the nearest commercial facility. The quantity of POTW wastewater applied to land at a given POTW will be given by the Needs Survey data base retrieval (see Step l.c). The quantity of sludge applied to land at a given POTW can be estimated from sludge generation factors provided In Table 34 In Section 6. (The quantity of sludge generated Is one output of Stage V for POTWs, Section 6.3.) b. If data for Steps l.b or l.c and/or Step 2.a are not available, proceed as follows. Consult the Needs Survey data retrieval (Exhibit H-l In Appendix H) to find out whether significant amounts of local sludge are known to be dried and shipped out of the area; If this Is the case, It cannot be tracked further. If this Is not the case, note that the cost of hauling makes It economically Infeasible for nonhazardous sludge to be transported In the wet state very far from the site of generation. Therefore, It can be assumed that all of the waste Is landspread close to the point of origin, and Stage V environmental release estimates can be based upon generalized climatological, soil, and geological data for the county. 4.3 Estimating Environmental Releases from Land Treatment - Stage V Decision Tree In Stage V, environmental releases from land treatment sites In the study area will be estimated using a mathematical model such as PRZM or SESOIL. In cases where there Is adequate site-specific Information, the model can be run for each site using the appropriate Input parameters. In many exposure assessments, however, many parameters will have to be estimated using methods presented In Section 4.1, and below. In such cases one or more model land treatment sites representative of the land treatment sites of Interest can be created and used In conjunction with available land treatment site population Information. Step 1 . Select an appropriate model for estimating environmental releases. Environmental releases to air, groundwater, and surface water will be calculated using a model such as PRZM or SESOIL. For nationwide or broad regional environmental releases estimates, consult Section 3.1.6 In addition to the following steps. 106 Step 2 . Identify Input requirements. The following types of data will probably be required for any relevant model: • Climatological data • Soil data • Chemical data • Geometric, application-specific data Climatological and soil data are available from standard data sources as described In Section 3.1.4. Chemical Information Is available from standard reference manuals. Geometric application- related and application-specific Information may be more difficult to obtain. As stated previously, the effort In this report focused on developing a few of the previously undeveloped and dlffIcult-to- acqulre parameters that are amenable to generic data. See Step 3 for suggestions on estimating the following parameters: • Groundwater level (Step 3.a) • Surface area of the site (Step 3.b) • Pollutant loading (Step 3.c) • Depths of soil zones (Step 3.d). Step 3 . Estimate relevant application-related and application-specific parameters, wherever appropriate. a. Depth to groundwater can be determined from statewide computerized data bases when these exist; see Section 3.1.4. In the absence of such data, an arbitrary value (or set of limiting values) can be selected on the basis of the Surface Impoundment Assessment (SIA) data base, soil maps, wetland distribution data for the subject state (see Section 3.1.4), or other general references. b. Surface area of the site may be available from the OSW Survey (USEPA 1983e), an HWDMS retrieval, or Information In state solid waste agency files for hazardous waste land treatment sites. See Section 4.1.5 for a detailed discussion of these sources of Information. If site-specific data on surface area are not available, determine whether data are available to estimate surface area using Equation 4-1 (Section 4.1.5). If this Is not possible, consider using the median surface area for hazardous waste sites In the U.S. 5.5 ha (13.5 acres), or consider computing the median size for the region or Industry of Interest In the assessment, using the data In Table 2, of Appendix A of USEPA 1983a. 107 The approach discussed above Is also recommended for land treatment sites receiving nonhazardous wastes. The recommended approach for estimating the surface area of land treatment sites handling POTW wastewater, In the absence of site-specific data, Is to multiply the facility capacity (mgd) by a value within the lower and upper limits of the range of application rates reported In Section 4.1 x .4 (40-240 ha/mgd). The surface area of sites receiving POTW sludges can be estimated In a similar manner, using the quantity of sludge generated (from Stage V of the POTW analysis or Table 34; Section 6) and the estimated application rate (140 - 230 kkg/ha, see Table 28 In Section 4.1.5) In Equation 4-1 (see Section 4.1.5). c. Pollutant loading (which will be based on the Stage IV estimate) can be expressed In several ways, depending on the nature of the disposal operation. For land treatment, It can generally be assumed that the pollutant Is well-mixed Into the soil, and pollutant loading can be expressed In terms of mass/area. The mass/area can be estimated using available Information on waste application rates, as discussed In Section 4.1.5. If Input data are measured concentra¬ tions In the soil at a land treatment site, then the area and depth of waste Incorporation (see Step 3.d) can be used In conjunction with the chemical concentration to calculate pollutant mass. d. Depth of soil zones will be determined using the same references that were mentioned for landfills In Section 3.1.4(4)(b), with the exception of the layer of waste Incorporation. Wastes may be plowed or Injected to a depth ranging from a few centimeters to 60 centimeters. The layer of Incorporation will usually constitute the upper unsaturated soil layer. Given the foregoing limitations, reliable environmental releases estimates may not be possible. If sufficient data have been compiled, proceed to Step 4; If not, proceed to Step 5. Step 4 . Using the model of choice, estimate environmental releases from each site receiving the waste; the chemical concentration In each soil layer can also be estimated If desired. The output of this step will be the following: • Flux or mass/area of subject chemical entering groundwater after the modeled period of time. 108 • Flux or mass/area of subject chemical volatilizing from the upper soil layer to the atmosphere after the modeled period of time. • Concentration and mass of the subject chemical In each soil layer after the modeled period of time. • Mass/area of the subject chemical lost due to surface runoff. Step 5 . If monitoring data are available, compare these with predicted concentrations. If estimated concentrations do not correlate with measured values, use best Judgment to evaluate the discrepancy. If the Input data are Insufficient to use a model, monitoring data (If available) may be the only available means of estimating environmental releases. Estimated environmental releases may be used as Input In the analysis of environmental fate and In the final exposure assessment, as discussed In Volumes 2 and 5 of this report. 109 5. SURFACE IMPOUNDMENTS This section contains the Information that will be the basis for the Stage IV and Stage V estimates for treatment, storage, or disposal of wastes In surface Impoundments. Surface Impoundments receive a large part of the Industrial and municipal liquid wastes generated In the U.S. Considerable site-specific Information on Impoundments Is available; however, estimating releases Is difficult because of uncertainty In the amounts of wastes In Impoundments and the movement of pollutants Into and through the groundwater. A discussion of general Information on surface Impoundments Is presented In Section 5.1. This text Is the basis for the Stage IV and Stage V decision trees given In Sections 5.2 and 5.3. 5.1 Background Information A surface Impoundment Is a natural topographic depression, man-made excavation, or diked area formed primarily of earthen materials designed to hold liquid wastes or wastes containing free liquids. Impoundments may serve the purpose of treatment, storage, or disposal of liquid wastes, and Include holding, storage, settling, and aeration pits, ponds, and lagoons. Depending on their design and purpose, surface Impoundments may lose liquids by one or more of the following processes: discharge to surface waters, evaporation, and Inflltratlon/percolatlon. Impoundments which do not discharge to surface waters are called nondischarging Impoundments even though losses occur through seepage and volatilization. A very common type of Impoundment Is the settling pond, which Is used to separate solids from liquids with or without the addition of chemicals to accelerate coagulation and precipitation. Many settling ponds are periodically dredged to restore them to original capacity. Other Impoundments are designed specifically to permit seepage Into the underlying aquifer. Impoundments that are not designed for seepage may serve as holding or evaporation ponds and are sometimes lined. See USEPA 1978 for a comprehensive description of uses and designs of Impoundments In the U.S. The size of Impoundments varies from a few tenths of an acre to hundreds of acres, and depths vary from 0.6 m (2 feet) to more than 9 m (30 feet) below the land surface. Depending on the function, Impoundments may be operated Individually or may be Interconnected so that flow moves from one Impoundment to another (Acurex 1980). The EPA classifies surface Impoundments Into one of five categories, depending on the origin and the type of wastes: municipal (l.e., water treatment, municipal sanitary landfill, and sewage treatment), Industrial, agricultural, mining, and oil and gas brine pits. Municipal no sanitary landfill Impoundments, sewage treatment plants, and Industrial Impoundments will generally be of greatest Interest because these are the types of facilities that are most likely to receive toxic wastes subject to regulation under TSCA; only the data pertaining to these types will be presented here. Fortunately, more Information Is available for these sites than for other types of Impoundments. However, the procedures developed here could also be applied to agricultural, mining, oil and gas, and water treatment Impoundments. Table 29 presents a summary of the estimated number of active Impoundments of each category. Most of the readily available Information on surface Impoundments comes from state agencies and the Surface Impoundment Assessment (SIA) conducted by the EPA Office of Drinking Water pursuant to Section 1422(b)(3)(c) of the Safe Drinking Water Act. The culmination of this effort Is several preliminary summary reports (Geraghty and Miller 1978, Sllka and Swearingen 1978, USEPA 1980e) and a computerized data base containing data on the numbers, locations, and potential effects on groundwater of Impoundments In the U.S., using a rating system described In Sllka and Swearingen (1978). Because of funding limitations, the SIA compiled data for only 80% of the Industrial sites, 55% of the sewage treatment sites, and 83% of the municipal sanitary landfill Impoundment sites nationwide (see Table 29); therefore, site-specific Information Is not available for many Impoundments. Furthermore, since the SIA was based on unverified secondary sources of data, It will be suitable as source Information only for large-scale exposure assessments where errors In or absence of site-specific data will not significantly skew the overall results. Some of the Information In the SIA Is confidential; therefore, retrievals may not give the owner or name of some facilities. Obviously, additional site-specific data would be necessary for exposure assessments where site-specific estimates of chemical releases are required. Other useful sources of Information on surface Impoundments Include the Needs Survey (Exhibit H-l In Appendix H) and the references on hazardous and Industrial waste disposal mentioned In Sections 2.3.3(4) and 2.3.3(5) and documented In Appendix C and Table D-5 of Appendix D. 5.1.1 Types of Impoundments Municipal sanitary, sewage treatment, and Industrial surface Impoundments serve different purposes and receive different kinds of waste streams. A brief summary of relevant features of each of these categories follows: (1) Municipal sanitary landfill Impoundments . The SIA located 179 sites containing approximately 446 Impoundments. Of the located sites, 149 were assessed. No description of the Impoundments In this category was given In the reports published to date, but It Is assumed that these 111 Table 29. Summary Statistics for Active Surface Impoundment Sites Located In the SIA Category Number of 1 oca ted sites Number of assessed sites Number of located impoundments* 3 1 ndustria 1 10,819 8, 193 25,749 Munlei pa 1 19,116 10,675 36,179 Agr(cultural 14,677 6,597 29,167 Mining 7,100 a 1,448 24,451 011 and gas brine pits 24,527 a 3,304 64,951 Other 1,500 327 5,745 TOTAL 77,739 30,544 176,242 a The number of mining and oil and gas brine pit sites is not necessarily related to actual ownership and (nay be different than the actual number of legal sites. The number of located impoundments would be a closer approximation for these two categories. ^Some sites have more than one surface impoundment. Source: USEPA 1980e. 112 sites generally receive partially dehydrated sludges from POTWs. Only 29.5% of the assessed sites had liners; the types of liners used are given In Table 30. Based on an EPA estimate, the typical size of this type of Impoundment Is about 1 ha (2.5 acres) (USEPA 1979b). (2) Municipal sewage treatment Impoundments . This type of Impoundment may be used to treat, store, and dispose of wastewater as well as sewage sludge. Based on the Needs Survey (see Exhibit H-l In Appendix H), the SIA located 18,189 sewage treatment plants with a total of 34,356 Impoundments. Of the located sites, 10,043 were assessed, and 22.8% of the assessed Impoundments were lined (Table 30) (USEPA 1980e). A variety of types of surface Impoundments are associated with the storage, treatment, and disposal of wastewaters. These Impoundments may be lined or unllned and may represent minor or major components of large treatment and waste disposal systems; they may also be the sole component. In primary treatment systems, Impoundments may be used for temporary storage, settling or disposal of wastewater by percolation and evaporation. In conventional secondary treatment plants. Impoundments may be used only for storage and settling; Impoundments may be the principal components of systems that consist mainly of anaerobic and aerobic waste-stabilization ponds. Another type of Impoundment used In secondary treatment Is the temporary holding or storage pond for disposal of effluent after secondary treatment. In some tertiary treatment plants, effluents are passed through shallow polishing ponds. In many wastewater treatment systems, wastewater Is ultimately discharged to streams rather than disposed of by evaporation or seepage (USEPA 1978). Impoundments at sewage treatment facilities are also used for the treatment, storage, and disposal of municipal sewage sludge. They are commonly used for temporary storage of sludge prior to ultimate disposal, for sludge stabilization prior to land application, or as permanent disposal for liquid, dewatered, heat-dried or composted sludge (USEPA 1980a). Shallow rectangular Impoundments with permeable sand bottoms are sometimes used for drying municipal sewage sludge. These "drying beds" may or may not have underdrains for leachate control. Impoundments that receive partly dehydrated sludge are usually covered and abandoned after being filled (USEPA 1978). Approximately 11% of the sewage sludge produced In 1978 was disposed of In such lagoons (USEPA 1980f). Table 6 In Section 2.3.3(2) presents more recent estimates on sewage treatment Impoundments. The size of sewage treatment Impoundments varies, but one EPA pub¬ lication assumed that the typical area Is 1 ha (2.5 acres) (USEPA 1979b). Oxidation ponds are generally 0.9 to 2.4 m deep, aerated lagoons are 2.4 to 4.6 m deep, and anaerobic lagoon systems are 3.6 to 5.2 m deep (USEPA 1978). 113 Table 30. Liner Data, Municipal Impoundment Sites 4- TD c © — — CM CM © C • • • • o — o o r- L. — r* r- © c CL 3 4- C *o O' in CO GO © © • • • • o c o O' CM CM L. — CM CM CM CM © •— Q_ L. © c © c in ON GO CM © 1 in r*^ L. CO —— —- -Q E © X L. © i vO m C ID ■ CO O' _J I in in t- © i VD *4 c CO CM CM — i in _l ■ % * ■ CM *o — © © c o GO *4 csi 4- — in O' CM S O — m VD o h- c * 3 in VD in © © 4- 4- © — •D in CM O' CM m L. m 00 VD — © —• CM CO © C «k •k 4- — r^* 0 •— h- © m CM o TD in in O O' O' O' U~) U ’U’ , d- E E © © 4- 4- CL in in © Q. >- >- 4- 3 in in 0 in 4- © © n i_ m U) 3 © 3 © 00 4- H— * © © © o: c/n © © C — © u O) — c >* * 4- © 4- — — © c ® *4- 't- ® g 1 ® > —• o XL — —— TD T3 > in — o © o 0 0. 4- Cl a. c E E © i_ © o © c TD 0) © L. i_ «k >- © © jQ XL CL f © N D in 4- 4- —« © > — 3 ® © © — © 4- 4- .c u l- c C C c c V © o © — 0 — l_ © © 4- —— — 1- L. 1- >> 4- E U XL © >« in £ © 0 © © © C 03 c Q. 4- — © CL -C — jC XI —— © .c o in © o 3 4- x: S 4- o CO o o < z Q_ 0- CO X UJ o o II II II It n II II II II II II II II II CM rn in vD r** co O' o — CM *4 in 114 Source: USEPA I980e (3) Industrial Impoundments . Many Industries treat, store, or dispose of liquid wastes In Impoundments. The design and function of Industrial Impoundments varies widely by Industry. Industrial Impoundments are typically used for evaporation, aeration, oxidation, recycling, Infiltration, stabilization, settling, disposal, and storage. Stabilization ponds are very common waste treatment systems at Industrial plants. In some plants auxiliary ponds serve for polishing (l.e., final treatment) and temporary retention of effluents from conventional activated sludge systems before discharge to streams. Ponds may also receive scrubber water and ash residues (See Section 2.3.3(1) and USEPA 1978). The size of Industrial Impoundments varies widely. One EPA document assumed that 95% of all Industrial facilities are approximately 1 ha (2.5 acres), the remaining 5% being 20 ha (50 acres) (USEPA 1979b). These figures, together with the range of depths presented In the description of municipal sewage treatment Impoundments form the basis for design estimates when site-specific data are not available or desirable. The SIA located 10,819 Industrial sites containing a total of 25,749 Impoundments. Of the 8,243 assessed sites, only 27.6% were lined (USEPA 1980e). See Tables 31 and 32 for the breakdown of surface Impoundment populations and liner characteristics by SIC Code. A recent compilation of HWDMS application data (Table D-7 In Appendix 0) Indicates that nationwide there are 1,366 facilities that treat or store hazardous wastes In surface Impoundments and 360 that dispose of hazardous wastes by surface Impoundments. 5.1.2 Environmental Releases from Surface Impoundments Chemical substances treated, stored, or disposed of In waste Impoundments may be released to air, surface water, and groundwater over time. Releases to air may occur via volatilization of organic gases and fugitive dust. Surface waters may be contaminated by permitted effluents, by sudden releases when dikes are breached or lagoons are washed out during periods of high surface runoff, or by leached contaminants. Finally, surface Impoundments without properly designed containment and leachate collection systems may cause contamination of groundwater resulting In human exposure through the consumption of well water or through seepage of groundwater Into basements and subsequent volatilization of toxic substances (Acurex 1980). The Information resources reviewed In the course of developing this methodology did not Include any models designed specifically to estimate environmental releases from surface Impoundments. See Section 3.1.3 for a general discussion on predicting environmental releases from land disposal sites. 115 Table 31. Distribution of Industrial Impoundment Sites by SIC Code SIC Code Type fact 1Ity Located sites Located Impoundments Assessed sites 20 Food 2,162 5,160 1,708 21 Tobacco 6 11 5 22 Text lie mills 268 536 210 23 Apparel 15 13 10 24 Lumber and wood 373 781 294 25 Furniture and fixtures 23 35 20 26 Paper and allied products 421 1,349 288 27 Printing and publishing 18 24 15 28 Chemical and allied products 1,514 4,577 1,276 29 Petroleum and allied products 696 1,984 537 30 Rubber and ml sc. plastics 156 252 129 31 Leather products 34 104 31 32 Stone, clay and glass products 723 1,343 630 33 PrImary metals 599 1,480 444 34 Fabricated metals 686 1,416 513 35 Mach 1nery 174 294 141 36 Electric and electronic 210 391 177 37 Transportation equipment 217 510 152 38 1nstruments 47 92 36 39 Ml sc. manufacturing 235 359 120 40-47 TransportatIon 320 516 238 491 Power plants 593 1,671 301 492 Gas production and dlst. 250 543 62 493 Combination elec/gas 39 81 36 496 Steam supply 17 35 13 4953 Industrial refuse sites 199 602 161 517 Petroleum bulk terminal 65 141 46 554 Service stations 50 65 44 721 Cleaning establishments 261 381 129 7542 Car washes 59 72 48 1389 Oil field services 276 764 96 07 Agricultural services 93 167 83 TOTAL 10,819 25,749 8,243 Source: USEPA 1980e Table 32. Liner Data Industrial Impoundment Sites Membrane SIC Code 3 Total Sites Liner Data Total Un11ned LIner b 2-3-4-15 Liner b 5-6-7 LIner^ 8-14 Percent 1 Ined Percent uniIned 20 1,337 981 299 24 33 26.7 73.3 21 4 4 0 0 0 0.0 100.0 22 151 112 24 4 11 25.9 74.1 23 6 5 1 0 0 16.7 83.3 24 257 165 84 6 2 35.8 64.2 25 14 10 3 1 0 28.6 71.4 26 253 153 75 3 22 39.6 60.4 27 12 11 0 1 0 8.4 91.6 28 1,012 647 222 44 99 36.1 63.9 29 446 319 103 18 6 28.5 71.5 30 114 91 12 6 5 20.2 79.8 31 27 22 3 1 1 18.6 81.4 32 498 386 80 24 8 22.5 77.5 33 402 275 85 17 25 31.6 68.4 34 453 357 62 12 22 21.2 78.8 35 113 75 24 6 8 33.7 66.3 36 154 112 20 8 14 27.3 72.7 37 131 98 22 5 6 25.2 74.8 38 30 22 3 1 4 26.7 73.3 39 105 89 11 3 2 15.3 84.7 40-47 187 129 43 9 6 31.1 68.9 491 375 243 102 11 19 35.2 64.8 492 49 32 9 3 5 34.7 65.3 493 34 26 7 0 1 23.6 76.4 496 13 11 1 1 0 15.4 84.6 4953 135 90 33 6 6 33.4 66.6 517 41 33 8 0 0 19.6 80.4 554 44 41 2 1 0 6.9 93.1 721 109 105 3 0 1 3.7 96.3 7542 39 35 3 1 0 10.3 89.7 1389 92 73 10 3 6 20.7 79.3 07 78 62 12 0 4 20.6 79.4 TOTAL 7,715 4,814 1,366 219 316 27.6 72.4 a See Table 31 for key to SIC codes. ^See Table 30 for key to liner types. Source: USEPA 1980e. 117 5.2 Allocating Waste Streams to Surface Impoundments - Stage IV Decision Tree In this stage, the user will evaluate available Information on the disposal practices of the subject waste generators, the types of Impoundments In the study area, and the waste characteristics In order to enumerate the Impoundments that are likely to receive the subject waste stream. The waste stream will be allocated to Individual sites using criteria tailored to the source and nature of the waste. The confidence In these estimates will vary depending on the source of the waste and the types of Impoundment. Step 1 . Determine whether disposal of the subject waste stream will be limited to certain types of surface Impoundments. As discussed In the Introduction to surface Impoundments, a variety of Impoundment designs are In use at both municipal and Industrial sites. Because of data limitations, It was not possible to develop a rule for estimating the types of Impoundments that can be found at a given site In the absence of site-specific Information. Therefore, this Information will have to be obtained from computer retrievals of the SIA, Needs Survey, and HWDMS data bases, as described below. These data bases can be used as a source of both generic and site-specific Information on Impoundment type. Step 2 . If applicable, determine the proportional distribution of the subject waste stream between on-site and off-site facilities. This knowledge will be helpful In Step 3, when Identifying Individual Impoundments that are probable candidates for disposal of the wastes. The degree of on-site versus off-site disposal In Impoundments varies depending on the type of waste. Separate procedures for estimating on- versus off-site disposal are given below for wastewaters, POTW sludges, hazardous waste, nonhazardous Industrial solid waste, and Incinerator residue. In general, however, off-site versus on-site disposal In surface Impoundments can be estimated In one of two ways: (1) using waste-specific or Industry-specific generic Information and (2) using site-specific Information. a. Wastewaters . All municipal and Industrial wastewaters treated at POTWs that use Impoundments for treatment, storage, and disposal are by definition disposed of off-site. Therefore, the percentage of wastewaters treated off-site will already have been determined In Stage III. It will be more difficult to determine the extent to which surface Impoundments are Involved 118 In the treatment of the Industrial wastewaters that are treated on-site because this Information Is not always available. The only direct source of Information on Impoundments associated with Industrial wastewater treatment Is the Surface Impoundment Assessment data base (SIA). As stated previously, however, this data base Is not complete. b. POTW sludges . Surface Impoundments used for the storage or disposal of POTW sludges will generally be located at the POTW facility. c. Hazardous wastes . The percentage of the waste treated, stored, or disposed of In surface Impoundments on-site can be very roughly estimated by examining waste-specific or Industry- specific disposal patterns reported In available documents listed In Section 2.3.3(4). (See Appendix C and Table 0-5 In Appendix D for examples of the kind of Information available In these documents.) Table 27 In Section 4, compiled from USEPA 1980b, suggests that actual disposal of hazardous wastes In off-site facilities may be restricted to only 11 facilities nationwide, all of which occur In EPA Regions IV, VI, IX, or X. These facilities handle only 1.3% of the hazardous wastes generated. Industry-specific Information contained In other documents, presented In Appendix C and Table D-5 In Appendix D, can be used In conjunction with Table 27 to decide whether It Is likely that the waste will be disposed of In off-site Impoundments. For Instance, If Table 27 Indicates that there Is no commercial hazardous waste facility using a lagoon for treatment, storage, or disposal In the vicinity of a manufacturing plant producing a waste that Is usually disposed of via surface Impoundments, It can be assumed that the waste Is handled on-site. Other sources of this Information are the Hazardous Waste Data Management System (HWDMS) (see Section 2.3.3(4) and Exhibit D-l In Appendix D) and the SIA data base. Retrievals from these data bases can Indicate three things: (1) whether there Is an Impoundment on-site at a given location, (2) what percentage of facilities of a certain type (e.g., manufacturers of organic chemicals) have on-site Impoundments, and (3) what percentage of commercial hazardous waste disposal facilities In the area of Interest use surface Impoundments for treatment, storage, or disposal. The site-specific and generic data derived from these data bases should be used to supplement the above-mentioned documents. d. Nonhazardous Industrial solid wastes . No known sources of compiled Information exist on the degree to which this type 119 of waste Is disposed of off-site In surface Impoundments, except for the Inventory of Impoundments compiled by Waste Age magazine (see Table 33). Until better data are available. It Is suggested that the same data sources be used as for Industrial hazardous wastes. The SIA should be particularly helpful because It will generally Indicate whether or not an Impoundment Is located on-site, regardless of whether the facility has filed an application for hazardous waste handling. The SIA may also be useful as a source of generic data If a retrieval Is done for the SIC code of Interest. e. Incinerator residue . If Impoundments are used for the storage or disposal of Incinerator wastes, It can generally be assumed that the Impoundment will be located near the site of Incineration. Step 3 . Based on the Information In Steps 1 and 2 and available Inventories of disposal facilities, Identify the Impoundments that are probable candidates for disposal of the subject waste. Consider the obvious constraints Imposed by the geographic area, the applicable types of Impoundments, and the disposal practices of Industry for the waste stream of Interest. All of the Information needed for this step will be available through the computer retrievals of the SIA and HWDMS data bases In addition to general documents on Industrial disposal practices. Separate decision trees are presented below for each of the different waste categories. a. Wastewaters . The Information compiled for POTWs from the Needs Survey data base (see Sections 2.3.3(3) and 6 and Exhibit H-l In Appendix H gives some Indication of whether surface Impoundments are used to treat, store, or dispose of wastewaters based on the treatments used at a given POTW. For Instance, the use of stabilization ponds, aerated lagoons, sludge lagoons, air drying lagoons, and seepage lagoons Is always associated with surface Impoundments. Additional Information can be gleaned from knowledge of the wastewater treatment methods used at the POTWs of Interest (given In the Needs Survey retrieval). However, the extent to which Impoundments are used for storage and In conjunction with types of wastewater treatment other than those listed above Is not always clear based on the Needs Survey computer retrieval. For this reason, the Needs Survey data should be supplemented using site-specific data retrieved from the SIA data base for municipal sewage treatment Impoundments. Even with the SIA data, however, there will not be site-specific 120 Table 33. Inventory of Pits, Ponds, and Lagoons from 1981 Waste Age Survey Number of pits, ponds, and EPA Region/ Number of pits, ponds, and lagoons Identified lagoons owned and operated by the Industry upon whose State In EPA's S1A a site they are located 3 Region tf I ConnectIcut 1,200 610 Maine 453 % 173 sites 177 Massachusetts 1,962 1,962 New Hampshire - - Rhode Island 45 45 Vermont - - Region #2 New York - - Delaware - - New Jersey 1,027 unknown Puerto R ico 379 379 VI rg 1 n 1 s 1 a nd s - - Region #3 District of Columbia 0 0 Maryland - - Pennsy1 van 1 a 33,401 1,645(+ 19,702 % oil & gas welIs V1 rg 1 n I a - - West Virginia - - Region #4 Alabama - - Florida 5,681 5,681 Georg 1 a - - Kentucky 340 - Mississippi 3,300 3,200 North CarolIna 5,717 unknown South Carolina - - Tennessee 1,500 648 Region #5 II 11 no Is 8,000 8,000 1ndlana 2,688 unknown Michigan - - Ohio 14,000 1,500 M1nnesota 3,365 415 Impoundments W1 scons 1 n 1,717 614 121 Table 33. Inventory of Pits, Ponds, and Lagoons from 1981 Waste Age Survey (contlnued) Number of pits, ponds, and Number of pits, ponds, lagoons owned and operated EPA Region/ and lagoons Identified by the Industry upon whose State _ In EPA's SIA a _ site they are located 9 Reg Ion #6 Arkansas 2,000 unknown Lou 1slana 2,881 916 1nd./IOI Mun./I New Mexico 2, 101 702 + 15,7 Texas 3,842 3,458 Ok lahoma 4,524 466 Region #7 Iowa - - Kansas 3,398 263 Mlssour 1 - - Nebraska 600 100 Region #8 Co lorado 1,900 unknown Montana - - Utah 660 unknown Wyomlng - - North Dakota - - South Dakota - - Region #9 Ar I zona 552 unknown Ca 11 torn I a - - Hawa11 - - Nevada 923 unknown Region #10 Al a ska - - 1 da ho - - Oregon 714 714 Wash 1ngton 1 ,047 466 Guam 102 102 TOTALS 109,839 69,490 a Blank denotes Information not available at the time of the survey. The SIA data base has a more up-to-date listing. Source: Anon. 1981c, Waste Age . Land Disposal Survey. 122 data for all surface impoundments because not all municipal Impoundments were Included in the SIA. Furthermore, the SIA assessments do not always indicate the type of lagoon. Therefore, it is recommended that the investigator consider using Needs survey and SIA retrievals to develop generic data on the type of Impoundments likely to be associated with various types of wastewater treatment as described below. If fairly accurate generic data are desired, the municipal Impoundment data from the SIA can be aggregated according to treatment (available through the Needs Survey retrieval). For example, the SIA municipal Impoundment data for all secondary POTW plants using activated sludge (as indicated by the Needs Survey data) can be analyzed to extract generic data on the average number of Impoundments per site, the average surface area of the Impoundments, and the type of Influent (primary, secondary, sludge, etc.). These generic data can be used for POTW plants for which the site-specific Impoundment data in the SIA are not sufficient to characterize the Impoundments. The level of detail and accuracy required by the exposure assessment will dictate whether the time spent comparing the SIA and Needs Survey information is justifiable. b. POTW sludge . The Needs Survey retrieval sometimes provides information on whether a given POTW disposes of its sludge on- or off-site and usually lists the treatment/disposal method used. The utility of the Needs Survey data base in determining sludge-handling practices at POTWs was discussed in Section 2.3.3(2). Use the Needs Survey retrieval to compile a list of POTWs that appear to use Impoundments In the sludge handling process. The fact that the Needs Survey does not always Indicate whether the POTW sends Its sludge to another facility for handling does not constitute a major data gap, because most POTWs that treat wastewater on-site also have a means of handling their own sludge (USEPA 1981e). c. Hazardous wastes . The determination of surface Impoundments likely to receive the waste of Interest will be based on the site-specific Information In the SIA and HWDMS data bases In addition to the general Information on Industry-wide disposal practices assembled In Stage III, and the information compiled In Step 2. First, assemble all site-specific Information retrieved from the HWDMS and the SIA data bases (this will already have been done In Step 2). Check to see which of the sites of interest have on-site surface Impoundments and which off-site commercial disposal facilities use surface Impoundments for treatment, storage, or disposal. Evaluate the Information on disposal practices for wastes similar to the subject waste (see Table 9 in Section 2) and other Information 123 listed In Appendix C and Table 0-5 In Appendix 0. From this material, compile a list of the sites which have surface Impoundments that are likely candidates for receiving the waste. d. Nonhazardous Industrial solid wastes . As stated In Step 2, there are no known documents that contain useful Information on the nonhazardous Industrial waste practices of Industries. Therefore, the Investigator should rely heavily on the SIA data base for Information on which sites might use on-site Impoundments for treatment, storage, or disposal of wastes. This Information should be supplemented with the generic Information on Industrial waste practices presented In Stage III (and Appendix C and Table D-5 In Appendix D), under the untested assumption that Industries will treat similar wastes In similar ways, regardless of whether the wastes are hazardous. Some Individual judgment will be necessary In deciding which off-site Impoundments are likely candidates for the subject waste. A retrieval from the SIA data base of all Industrial Impoundments In the area of Interest may provide the Investigator with some clues as to which have off-site facilities. For example, the name of the owner and auxiliary Information on the types of wastes handled may Indicate whether any commercial disposal facilities In the area operate Impoundments. Assuming that hazardous waste practices are similar to nonhazardous waste practices. It Is unlikely that off-site disposal In Impoundments Is very common. An exception to the rule may be off-site disposal of nonhazardous Industrial wastewater treatment sludges via off-site POTW sludge handling facilities. This Is not a widespread practice, however; currently only five POTWs, located In California, Delaware, Louisiana, and Texas, handle such sludges (USEPA 1981e). A Needs Survey data base retrieval could provide site-specific data on these facilities, If required. e. Incinerator residue . See Section 2.3.3(1) for Information on disposal of ash In lagoons. If ash Is disposed of In lagoons (which may not be readily determined), assume that the lagoon will be at the site of the Incinerator. The Incinerators that have on-site lagoons may possibly be Identified by comparing the data from the SIA data base retrieval with Incinerator Inventories (see Appendix I, Tables 1-2, and 1-3). Assume that the Incinerators with on-site lagoons use them for ash disposal. Step 4 . Quantify the amount of the subject waste handled by each disposal site Identified In Step 3. Check to see whether there Is Information on the capacity and current operating characteristics (e.g., types of wastes 124 handled) for the sites listed In Step 3. If so, use this Information In conjunction with available Information on the disposal practices of the source(s) of the waste disposed of at each facility to allocate wastes to each site. If not, allocate the waste according to some other method (e.g., equal distribution to all candidate sites). The output from Stage IV for assessments requiring site-specific estimates of environmental releases will be a list of candidate sites and the amounts of the subject waste disposed of at each site. The primary sources of data for this step are the SIA, HWDMS, and Needs Survey data bases. Additional useful generic Information can be derived from previously cited documents pertaining to surface Impoundments. Separate discussions on how to allocate amounts of waste to Individual sites are presented below for wastewaters, POTW sludges, hazardous wastes, nonhazardous wastes, and Incinerator ash. a. Wastewaters . For all of the municipal Impoundments listed In Step 3, one can obtain the current POTW plant flow from the Needs survey data base retrieval. This Information, coupled with any available site-specific data relating to capacity given In the SIA, will provide a basis for estimating the maximum amount of waste treated, stored, or disposed of at the Impoundment of Interest. See Section 6.2 to find out how to estimate how much wastewater Is treated at a given POTW. This represents the maximum amount of the waste that might be treated, stored, or disposed of In the POTW surface Impoundments. Based on additional generic or site-specific data retrieved from the SIA data base, this maximum estimate can In some cases be refined to reflect the amount that Is really being handled by the surface Impoundments. In most cases, however, the Investigator will have to assume that all of the wastewater treated at the POTW will pass through or be disposed of In the Impoundments. b. POTW sludge . Using the list of POTWs that are likely candidates for the treatment, storage, or disposal of sludge In surface Impoundments (Step 3) In conjunction with site-specific Information from the SIA data base, the percentage of the waste that goes Into Impoundments can be estimated, as described below. The Needs Survey data will Indicate which sludge disposal practices are used and thus will provide Information on the type of Impoundments used and whether they are for treatment, storage, or ultimate disposal. The site-specific SIA data will sometimes augment the Needs Survey Information by giving the number of surface Impoundments, the type of waste 125 (e.g., sludge, wastewaters), and the purpose of the Impoundment (whether It Is for treatment, storage, or disposal). If the site-specific SIA data are Insufficient to determine the number of Impoundments Involved In sludge handling, use Individual Judgment based on the Needs Survey data to estimate how much of the sludge Is handled In surface Impoundments, and whether the Impoundments are used for treatment, storage, or disposal. c. Hazardous wastes . The allocation of hazardous wastes to Individual Impoundments will be based largely on data retrieved from the HWDMS data base supplemented by Information from the SIA data base. Use the list of probable sites compiled In Step 3 as the basis for the allocations. Data from the HWDMS retrieval will Indicate which plants have on-site Impoundments that handle hazardous wastes. Unless competing hazardous waste handling methods are practiced on-site, assume that all of the on-site generated waste Is handled In the surface Impoundments), providing that the capacity of the Impoundments (given In the HWDMS retrieval) Is sufficient to handle It. In the case where other disposal methods are available on-site (as Indicated by the HWDMS retrieval) review the available documents on waste disposal for the Industry of Interest (see Section 2.3.3(4), the tables In Appendix C and Table D-5 In Appendix D), paying particular attention to the disposal methods commonly used for similar wastes. If some of these methods are also available on-site, then use best Judgment to allocate the waste between treatment In surface Impoundments and the other waste handling methods. If any off-site commercial hazardous waste facilities with surface Impoundments were listed In Step 3 as probable candidates for receiving the waste, then use best Judgment to allocate the waste to the most appropriate site. As stated previously, however, off-site surface Impoundments are not often used for handling the hazardous wastes from most Industries. After the Initial allocation of subject waste quantities to Individual surface Impoundments Is complete, be sure to evaluate these estimates In light of the original Stage III estimates for all disposal methods, as suggested In Section 2.3.3. d. Nonhazardous Industrial solid waste . Use the list of probable Impoundment sites from Step 3. Proceed as for hazardous wastes, except that the SIA rather than the HWDMS will be the major site-specific source of data. Because there will not always be site-specific Information on competing treatment/storage/ disposal methods for nonhazardous wastes (unless there are data on landfills, etc., provided by the 126 states), It will be more difficult to evaluate the likelihood that the subject waste Is handled on-site by methods other than surface Impoundments. Considerable Individual judgment will be required In this step. In general, however, assume that all of the waste generated on-site Is handled by Identified on-site Impoundments If the subject waste Is similar to wastes frequently handled by this method. e. Incinerator residue . Based on the Information presented In Section 2.3.3(1), It Is reasonable to assume that all of the Incinerator residue generated on-site Is disposed of on-site. Therefore, In the absence of Information to the contrary, assume that Incinerator sites with on-site surface Impoundments dispose of all of the Incinerator residue In the Impoundments. 5.3 Estimating Environmental Releases from Surface Impoundments - Stage V Decision Tree This stage Involves the estimation of releases to air, surface waters, and groundwater from surface Impoundments. First, the user characterizes the design/operating features of the subject Impoundments with respect to parameters that affect releases. Then, these site- specific parameters are used In conjunction with the waste Input (from Stage IV) as Input parameters In an appropriate model(s) to estimate releases. This study Identified no comprehensive models tailored to estimating releases to all environmental media from surface Impoundments. For large-scale assessments, the SIA data base can be used to generate generic data on typical or representative sites together with data on the number of facilities. See Volume 1 of this series for a discussion of this approach to exposure assessments. Step 1 . a. Identify and list the Important design and operating characteristics of surface Impoundments that affect releases to the environment. A number of design factors of surface Impoundments affect their ability to release chemical substances to the air, groundwater, and surface waters. The most Important of these are listed below. • Liner. The potential for groundwater contamination Is largely a function of the type and condition of liner used (If any). In order to function properly, the liner must be compatible with the Impounded wastes and free of defects. Breaks or leaks In liners will obviously result In escape of Impounded wastes Into the soil beneath the Impoundment, Increasing the potential for contamination of groundwater. 127 Currently there are no statistics on the probability of liner leakage as a function of liner type and age. For detailed discussions of the complex relationship between liners, Impounded wastes, and seepage, see USEPA (1983b), Stewart (1978), and Acurex (1980). • Cover. Surface Impoundments with covers will generally allow less volatilization than those without covers. Although no statistics were found on the percentage of Impoundments with covers, the available literature suggests that the use of covers In active surface Impoundments Is very rare. • Surface area. The nature of volatilization and seepage Is such that the surface area of the Impoundment affects releases; therefore, the larger the area, the greater the emission rate of volatile compounds. • Thickness of the unsaturated zone. The unsaturated zone Is the depth from the base of the Impoundment to the water table. The potential for the contamination of groundwater may Increase with decreasing thickness of the unsaturated zone, because pollutants attenuate to varying degrees as they migrate down through the unsaturated zone. • Type of subsoil In the unsaturated zone. This factor Is an Important determinant of the potential for groundwater contamination because pollutant attenuation depends In part on the characteristics of the soil. Including sorption character and permeability. • Thickness of the saturated zone. This parameter affects the ability of the groundwater to transmit water. • Type of earth material In the saturated zone. This parameter also affects the ability of the aquifer to transmit groundwater. • Amount of freeboard (l.e., vertical distance between level of liquid and top of berm or dike) In the sides of the Impoundment. An Impoundment with considerable freeboard will have a lower probability of flooding onto adjacent areas during periods of heavy precipitation than one with little or no freeboard. The amount of freeboard Is also related to the maximum surface area of the Impoundment. • Effluent to surface waters. Obviously, an Impoundment that discharges continuously or Intermittently to surface waters has the potential to contaminate the receiving stream. 128 It should be stressed that the preceding list Includes only the most Important parameters; the Interaction of these factors creates a complex problem In predicting releases that has not been solved to date. b. Determine which of the parameters listed In Step l.a are known for the sites of Interest based on accessible computerized data or other readily available Information. The SIA data base Includes some of the relevant parameters on a site-specific basis for those surface Impoundments for which a complete assessment was conducted (see Section 5.1). However, when the data base was created, some parameters were grouped Into categories for the purpose of rating the sites as to potential for groundwater contamination, and the "raw" data were not Included In the data base. Therefore, the data can only be extracted as ranges. The following Is a summary of the data (Sllka and Swearingen 1978). Refer to Tables G-l and G-2 In Appendix G for the relation between the rating and the raw data. • Thickness of the unsaturated zone. This parameter Is classified Into one of five categories ranging from 1 m to greater than 30 m. • Earth material for unsaturated zone category. This parameter Is classified Into one of three categories ranging from material with a permeability of 2 gpd/ft 2 to 0.02 gpd/ft 2 . » Thickness of saturated zone. This parameter Is placed In one of three categories ranging from 3 to 30 m. • Liner. The assessments often Include Information on whether a liner Is present and on the type of liner. Liner types Include: clay, modified bentonite, chemically modified clay, concrete, asphalt, metal, polyethylene, plasticized PVC, butyl rubber sheeting, chlorinated polyethylene. t Size. Another auxiliary parameter that Is sometimes Included In the site-specific assessments Is the size of the Impoundment. The Information sources reviewed for this methodology were not clear as to whether the size Is reported as area, capacity, or depth. Surface areas may be estimated If capacity and depth are known or estimated. The following parameters are sometimes available In accessible form from sources other than the SIA data base: 129 • Capacity. For hazardous waste Impoundments the capacity will be listed on the RCRA hazardous waste treatment/storage/ disposal (TSD) permit application (see Section 2.3.3(4) and Exhibit 0-1 In Appendix D) and will be entered In the HWDMS data base. • Effluent characteristics. If the surface Impoundment has a NPOES permit (see Exhibit H-2 In Appendix H) to discharge Into surface waters, the effluent volume may be available in the Industrial Facilities Discharge (IFO) file (see Section 6 and Exhibit H-2 In Appendix H). However, If the facility has other outfalls In addition to the surface Impoundment outfalls, It may not be clear from the IFO printout which flow corresponds to the surface Impoundments. c. Decide which of the parameters listed In Step l.a but not Step l.b (l.e., parameters that are useful but not readily available) can be obtained from existing files at regional EPA offices and state solid waste agencies. All parameters listed In l.a are sometimes available from agency files. The RCRA Part B permit application may contain much of the site-specific Information related to pollution potential for hazardous waste surface Impoundments. However, there are presently no plans for computerization of the Information contained In these applications, so these data will generally have to be retrieved manually from the EPA regional offices. Many of the parameters may be Included In state permit files, depending on how comprehensive the state's records are. See Section IX of USEPA 1978 for a summary of state policies and regulations regarding surface Impoundments. Step 2. a. Select the most appropriate model for predicting releases based on design/operating characteristics of the surface Impoundments and the characteristics of the Impounded wastes. The Ideal model for predicting environmental releases from surface Impoundments would be multimedia and would Incorporate the biological, chemical, and physical processes that occur within the Impoundment, such as biodegradation and sorption; It would also Include provisions for the effect of liners on releases to groundwater was Identified In the Information resources consulted In developing this volume. No such model, was Identified In the Information resources consulted to develop this volume, although the SESOIL model developed by Arthur D. Little Inc. for the EPA Office of Toxic Substances Is potentially adaptable for this purpose. See Section 3.1.3 of this report and Volume 5 of this methods development series for a more detailed discussion of modeling considerations. \ 130 A set of equations for estimating releases to air from surface Impoundments Is presented In Hwang (1982). These equations consider the following parameters: • Chemical properties of the Impounded substance • Concentration of the substance • Surface area of Impoundment • Overall mass transfer coefficient (based on the equilibrium constant, the liquid-phase mass transfer coefficient, and the gas-phase mass transfer coefficient). This model estimates the release rate In grams per second. The most difficult parameter to estimate when using this model Is the concentration, which Is not usually available for existing facilities and difficult to estimate accurately In proposed facilities. b. Determine which site-specific design/operating parameters are required to predict releases from surface Impoundments; consider whether there are "default" values for these parameters that can be used In the absence of site-specific data. Estimating releases from surface Impoundments generally requires numerous climatological, soil, chemical-specific, and site-specific data. The following procedures provide guidance on how to acquire data for a few parameters for which generic data have not been previously compiled. • Surface area of the Impoundment (m 2 ). When site-specific Information on the area of the Impoundment Is not available (either In the SIA or EPA/state files) assume that the average area of most Impoundments Is 1 ha (2.5 acres). Alternatively, do a retrieval of the SIA data base to obtain representative capacity data for the appropriate type of Impoundment (e.g., municipal sewage treatment, Industrial, etc.) that can be used as surrogate data. Obviously, If the capacity (volume) and the depth of the Impoundment are available on a site-specific basis, the area can be calculated, thus avoiding the need for surrogate values. • Depth to groundwater (m) . As stated previously, this will be roughly available through the rating system for surface Impoundments that were Included In the SIA data base (see Section 5.1). For those that were Included, there are at least two options: (1) Go to the sources of original data 131 recommended In the SIA documentation (USEPA 1978), or (2) retrieve relevant data for other surface Impoundments In the vicinity of the slte(s) of Interest, and use those data to estimate the depth of the unsaturated zone. • Depth of the upper, middle, and lower soil zones . The data In the SIA are not sufficiently detailed to deduce differences between the various soil layers; therefore, unless site-specific data can be obtained manually from state or EPA files, or from sources mentioned In USEPA (1978), assume a uniform unsaturated soil layer, with no distinguishable upper, middle, or lower soil zones. • Total volume of Impounded liquid wastes . Volume data can be calculated from the depth and surface area on a site-specific basis from the SIA or HWDMS data bases (assume capacity = volume). Alternatively, If resources permit, capacity Information could be obtained manually from state or EPA permit files. If no site- specific data are available, use surrogate data obtained by a computer retrieval (SIA or HWDMS) of capacity data for Impoundments expected to be similar to the Impoundments) of Interest. As a last resort, calculate volume, assuming that the area Is 1 ha (2.5 acres) and that the depth Is within the range given below, depending on the type of Impoundment (USEPA 1978). If the type of Impoundment Is not known, one may assume a depth of 3.8 m, which Is midway between the lowest and highest values listed. Aerated lagoon: 2.4-4.6 m Oxidation pond: 1.9-2.4 m Anaerobic lagoon: 3.5-5.2 m • Concentration of subject chemical substance In the Impounded liquid (mass/volume) . This parameter can be estimated using knowledge of the mass of the chemical substance In the Impounded waste (from Stage IV) In conjunction with the total volume of Impounded wastes (see above). A simple dilution calculation can be used, as follows (Equation 5-1). C = M (5-1) V where C = concentration of subject chemical In Impounded waste M = mass of chemical In Impounded waste V = total volume of Impounded waste. 132 • Pollutant loading In each soil zone (mass/area) . This parameter, which will be required by any applicable model, will be based on the concentration of the subject chemical In the Impoundment, which will In turn be based on the output of Stage IV, Step 4 (waste volume and concentration) and the total volume of Impounded wastes (determined as above). The exact method of deriving pollutant loading will depend on the model requirements and on whether the Impoundment Is lined. In the cases where monitoring data exist for the Impoundments) of Interest, this data can be used In place of estimated concentration. Step 3 . Estimate releases to air, surface waters, and groundwater from each surface Impoundment handling the subject waste, using an appropriate model. The exact output of this effort will depend on the model(s) selected. Step 4 . If monitoring data are available, compare with predicted concentrations. If estimated concentrations do not corroborate measured values, use best Judgment to evaluate the discrepancy. If applicable, calibrate the model and rerun. See Volumes 1, 2, and 5 of this series for guidance on completing the exposure assessment. Very few monitoring data are available for surface Impoundments. Monitoring data for some sites are Included In the auxiliary Information In the SIA data base; a retrieval from that data base would Include such data when they exist. However, these data are highly variable with regard to both quality and quantity. Monitoring of surface Impoundments Is required under RCRA. Unfortunately, there are no plans to computerize this data, which Is available only through Individual states or EPA regional offices. 133 6. PUBLICLY OWNED TREATMENT WORKS (POTWs) Public sewage authorities collect and treat residential, commercial, and Industrial wastewaters, as well as groundwater seepage and storm waters. Their capabilities range from collection without treatment to collection with advanced wastewater treatment. Exposure to chemical substances from POTWs can occur via the discharge of treated or untreated municipal wastewaters to surface waters or to groundwater, by volatilization of chemicals during treatment, and through treatment and disposal of sludges. Background Information on POTWs Is given In Section 6.1. Section 6.2 comprises the Stage IV decision tree, and Section 6.3 discusses Stage V. Information on computer retrievals of POTW data Is Included In Section 6.1. In general, there Is considerable Information available on the location and design of POTWs, less Information on chemical Inputs to POTWs, and limited tools for predicting releases of specific chemicals from POTWs. Some monitoring data are available. 6.1 Background Information Information on municipal wastewater treatment by POTWs, occurrence of chemicals In sludges and wastewaters, and tools for estimating environmental releases are discussed below. This section provides the Information base for the Stage IV and Stage V decision trees. 6.1.1 General A variety of treatment types are currently In use at municipal treat¬ ment plants (POTWs) nationwide. Regardless of the treatment type, however, POTWs usually operate 24 hours per day. Wastewater treatment plants can be categorized Into the following general classes, depending on the degree of treatment: preliminary, primary, secondary, and tertiary. Effluents discharged from plants that have preliminary treatment are considered "raw" wastewater. Preliminary treatment Includes comminution, screening, and grit removal. Primary treatment goes beyond this to remove most settleable solids. Eor regulatory purposes, It Is defined as producing effluent that does not meet secondary treatment standards; conventional primary treatment, generally provides preliminary treatment plus primary sedimentation. Advanced primary treatment Includes some biological treatment as well (Culp 1979). Secondary treatment consists of preliminary plus biological processes with no additional process except disinfection. Biological processes Include treatment by trickling filters, activated sludge, and rotating biological contactors. Advanced secondary treatment consistently provides effluents with low biochemical oxygen demand (BOD) (24-10 mg/1) 134 and the removal of nutrients, phosphorous, and/or ammonia. Tertiary treatment Is defined In terms of the effluent BOD and the removal of nitrogen; tertiary plants must consistently produce effluent with a BOD less than 10 mg/1 and have specific processes that can remove more than 50 percent of the total nitrogen present In the Influent wastewaters (Culp 1979). finally, the "no discharge" category Includes lagoon systems designed for evaporation and/or Infiltration. To a lesser degree, wastewaters In this category are treated by recycling, reuse, spray Irrigation, or groundwater recharge. Surface Impoundments are associated with many wastewater treatment processes and may be used for storage, treatment, or disposal (USEPA 1981e). By mandate of the federal Water Pollution Control Act (fWPCA), there Is a large body of readily available data on municipal wastewater collection and treatment that will aid In the assessment of exposure to toxic pollutants from this source. In particular, the annual Needs Survey conducted by the Priority Needs Branch of the EPA Office of Water Program Operations provides a wealth of both site-specific and generic data In the form of computer retrievals and publications. The national summary of municipal wastewater treatment presented In Table 7 In Section 2.3.3(3) Is derived from the 1980 Needs Survey (USEPA 1981e). A total of about 97,117,000 m3/day of wastewater was treated by POTWs In 1980. Of the 30 percent of the U.S. population not served by public sewage authorities, the majority Is probably served by on-site septic tanks or leachflelds; however, the Needs Survey does not give this Information. This report does not consider disposal of wastewaters on-site. Nationwide, about 83 percent of wastewaters treated by POTWs are of domestic (residential or commercial) origin, the balance being contributed by Industrial plants (USEPA 1981e). The extent of Industrial wastewater treatment by POTWs varies widely from locality to locality, ranging from treatment plants that receive no Industrial effluents to plants that are operated jointly by a sewage authority and an Industry, treating a large volume of Industrial wastewaters. The degree to which Industrial wastewaters are discharged Indirectly (l.e., via POTWs to surface waters) depends on many factors, Including the treatment capability of the local P0TW, the nature of the Industrial wastewaters, cost considerations on the part of both the Industry and the sewage authority, and federal and state policies and regulations. The EPA Is developing pretreatment standards applicable to a number of Industries that discharge to POTWs. 135 6.1.2 Chemical Substances in POTW Effluent and Sludge Metallic and nonvolatile organic compounds In the Influent wastewater to POTWs can accumulate In the sludge. The extent of this accumulation depends on the chemical properties of the substance. Its concentration In the Influent stream, and the design and operating characteristics of the plant. A portion of the more volatile organic chemicals Is lost to the atmosphere during treatment processes. The balance of the chemical Is generally discharged with the plant effluent to surface waters (and sometimes groundwater). Some toxic substances, most notably several chlorinated hydrocarbons, are formed during the treatment process (Burns and Roe 1982); other substances may undergo biotransformation (USEPA 1979c). The Effluent Guidelines Division (EGD) of EPA has undertaken a study of priority pollutants In POTW Influent, effluent, and sludge, based on sampling of 50 different plants (Burns and Roe 1982). The results provide Information on removal efficiencies of the priority pollutants detected. Tables H-l through H-7 In Appendix H give the summary statistics from the study, Including concentrations of priority pollutants In Influent, secondary effluent, and raw sludge, as well as percent removal by various treatment methods. In the absence of more reliable data, these results can be used as surrogate data to estimate removal efficiencies of other compounds with similar chemical properties. 6.1.3 Predicting Releases of Chemical Substances from POTWs Some attempts have been made to model POTW processes, but this study has not identified any validated models that can accurately predict releases to air, water, and sludge based on Influent concentration for the range of available wastewater and sludge treatment processes. The Monitoring and Data Support Division (MOSD) of the EPA Office of Water Regulations and Standards has developed a POTW model that might be adaptable to the needs of some exposure assessments. This model predicts the releases of priority pollutants to surface waters and to sludge based on the following variables: (1) known or estimated Influent concentrations and flow; (2) estimated removal efficiency; and (3) estimated loss through volatilization. The removal efficiencies are based on the POTW study of Burns and Roe 1982. This model Is already connected with the Industrial Facilities Discharge (IFD) file (see Section 2.3.3(3) and Exhibit H-2 In Appendix H), which facilitates modeling of the aquatic transport and fate. The model Is very limited, however. In that: (1) It does not model releases to air; (2) It predicts aqueous effluent releases for only priority pollutants; and (3) It models only one treatment configuration (typical secondary treatment). Ideally, a POTW model for exposure assessments would predict toxic substance concentrations and total waste volume for releases to air, effluent water, and sludge, based on treatment (Including sludge treatment). It 136 would take Into account the Inhibitory effects that high concentrations of certain toxic chemicals have on treatment efficiency and would consider the wastewater of Interest In the context of the total Influent flow to the POTW. In the absence of a model, there are some available data that may be used to predict environmental releases. The Needs Survey (described In detail In Exhibit H-l In Appendix H) contains site-specific Information on flows, treatment type, and populations served, and can be accessed by computer. The Needs Survey report (USEPA 1981e) provides the per capita domestic wastewater generation rate which Is 479 1Iters/caplta/day nationwide. (Domestic wastewater Includes both residential and commercial wastewaters.) The Needs Survey provides both site-specific Information and generic data. Together with the sludge generation factors given In Table 34, these data can be used to estimate effluent flow, as well as volume of sludge generated at a particular plant. The removal efficiencies and concentrations of some chemical substances In the sludge and POTW effluent may be very roughly estimated using the data In Tables H-l through H-7 In Appendix H for priority pollutants and possibly for chemicals that are structurally similar to the priority pollutants studied. The typical moisture and solids content of a sludge after various treatments can be estimated from data in Table 35. Finally, as a result of the National Pollution Discharge Elimination System (NPDES), some site-specific Information on flow and concentrations of toxic chemicals In effluent Is available for all major Industries that discharge to POTWs. The flow and Standard Industrial Classification (SIC) codes of plants belonging to one of the 21 major Industries (see Table D-8 In Appendix 8) that discharge Indirectly are available from the Industrial Facilities Discharge (IFD) file (see Appendix H), along with the NPDES permit number of the POTW to which they discharge. Thus, for any given POTW, the Identity of the major Industrial contributors Is readily available; conversely, for a known plant, the POTW to which It discharges (If any) Is easily learned. The EPA Office of Toxic Substances (OTS) Is sponsoring a project to tabulate frequency distributions of (1) POTW plant flows, (2) receiving stream flows, and (3) dilution factors for all POTWs In the IFD data base. These frequency distributions will be Invaluable tools In nationwide exposure assessments Involving releases of chemicals from POTWs. Monitoring data on POTW effluents and sludges are not available for many plants, and any available data will usually be limited to priority priority pollutants. The POTW study conducted by EGD (Burns and Roe 1982) contains site-specific monitoring data for 50 "typical" POTWs In the U.S. It also provides data on the reduction of priority pollutants 137 CT © C in •— t. c © •— O © O £ CT © >* c CT V © i_ 4- •— C — > K) CM o © 4- © 4— lO co • £ CT C 4- in • • — © TD t o © © O O o L. D K'l 13 * Cl w — E CT © P o o in \ TD o in — 4- CT © o — CM CM TD CT L. • • • CT © “O © TD o o O C 4— •k 4- C •— in 4- _ *+- © c O c in © © CL © © p E L_ 0 4- u o © in © L. © o h- c CT) c O in l- >* C O in in CT © © 4- •— m o L. •— +- — 4- (SI m m © 4- © 4- © © • • ^r TD — C 4- L. o o • C 4- © © © © o 13 C +- D * C © in CT © .— ID m in D © ■o u in o © CT © c o o — jC • ct •— • • • © c c T3 © o o o T3 JI O •— 13 4- TD C 4- •— — c © 4- in CO © © m t. in TD © o Cl © CT 4— •— > •— <_> JC o TJ © U E lx. © * O /-X O © o 4- in L. l_ 4- JO — *-N — © © © 4- o c CO CO JC © C i- 0 • • 4- c © © © o • o *— in © c D © 4- o CL © CT c in •— t. 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D L. o J= o © o D h- CL li_ CL 5 O © JD u CO 138 Table 35 Solids Content In Sludges in Relation to Treatment Sludge treatment Sol ids content % Comments Raw primary sludge after thickening 1-3 Conditioning, which occurs prior to thickening or de¬ watering, does not change solids content appreciably. Raw secondary activated siudge after thickening 0.5-1 3-6 Sludge stabilization (aerobic or anaerobic digestion) See comment Converts 50? of organic solids to liquid and gas forms. Dewatering in sandbeds 45 Occurs after digestion. After 6 weeks of drying solids, content may be as high as 85-90?. In the past, was the most popular method of dewatering. Vacuum filter 15-30 After this process, sludges can be placed in landfills, landspread, or incinerated. Currently, the most popular method of dewatering. Pressure filtration 40-50 Not widely used in U.S. Source: Culp 1979. 139 effected by Individual treatment processes. The Permit Compliance System (PCS), a computerized data base maintained by the EPA Office of Water Enforcement and Permits, contains effluent sampling data for the major NPDES permit holders, Including major municipal treatment plants. However, data are generally limited to conventional and selected priority pollutants. Limited additional data may be In the NPDES files at EPA regional offices or In the corresponding state agency files. Some of the states that have their own NPDES programs may have computerized data bases containing effluent Information for permits. 6.2 Allocating Wastewater to Individual POTWs - Stage IV Decision T ree The output of the Stage IV decision tree depends on the scope and depth of the assessment. At the greatest level of detail. It will provide a list of all POTWs that are probable candidates for disposal of the subject wastewater, together with their Individual capacities and current operating characteristics. For more general assessments, It will provide for each POTW treatment configuration of Interest estimates of (1) the typical quantity of the subject waste stream treated per plant and (2) the number of plants (If needed In the exposure assessment). The latter Information may be provided on a nationwide basis or may be limited to the POTWs of a specific region or those receiving the wastewaters of a specific Industry segment (Identified by SIC code). There Is a considerable body of fairly reliable data for this decision tree. Note that In the case of detailed assessments requiring computer retrievals, Stage IV will usually be performed along with the Stage III decision tree for wastewater as a single Integrated operation. In order to evaluate the potential for environmental releases from treatment, storage, and disposal of wastewaters In surface Impoundments, deepwell Injection, or land treatment of wastewater, the user will have to consult the Information In Sections 4 and 5, as well as this section. Keep In mind that the Information on how a POTW treats Its wastewaters and sludges and on the characteristics and quantities of waste generated will come from this section. In order to find out what happens to toxic chemicals In wastewaters that are landspread, placed In surface Impoundments, or deep-well Injected, see Sections 4, 5, and 8, respectively. Step 1 . List the POTWs that are probable candidates for disposal of the subject wastewater together with their capacities and current operating characteristics. (See l.a for domestic wastewaters and l.b for Industrial wastewaters.) 140 a. Domestic wastewaters . If the assessment Is nationwide In scope, then all of the POTWs In the U.S. are to be considered. Instead of compiling a list, consult Table 7 for a breakdown of the nation's POTWs by treatment types. Alternatively, use the data compiled by OTS on the frequency distribution of POTW flows In the U.S. (see description In Section 6.1). For assessments of regional or statewide scope, consult the annual summary of Needs Survey data base (USEPA 1981e). This provides POTW flow rates and treatment type breakdowns for each state. Summaries from the Needs Survey of the treatment populations and domestic flows by state are provided In Tables D-l and D-2 In Appendix D. For assessments requiring site-specific data, a computer retrieval from the Needs Survey data base Is recommended (Exhibit H-l In Appendix H). This can provide not only the proportion of the subject wastewater treated by POTWs (the usual output of Stage III for wastewater), but also (1) a list of the Individual POTWs In a specified county, sewer district, or other local area; (2) the capacity and current flow of each listed POTW; and (3) the type and level of wastewater treatment employed at each listed POTW. Thus, a single retrieval should suffice for both stages. At the same time, data may be retrieved on treatment methods employed for sludges (see Step 2). b. Industrial wastewaters . If the assessment is nationwide In scope and the Industry Is widespread, then almost all of the POTWs In the U.S. are to be considered. Therefore, Instead of compiling a list, consult Table 7 for a breakdown of the nation's POTWs by treatment types. If greater geographic resolution is required, a computer retrieval from the IED data base Is recommended (see Exhibit H-2 In Appendix H). In this case, Stages III (for wastewater) and IV (for POTWs) are usually performed together as one operation. For Industry-wide assessments, the data base may be accessed by SIC code; a geographic limitation can be superimposed on this If desired. The retrieval will Identify each receiving POTW with data on flow. For Information on all POTWs receiving Industrial wastewaters In a given area, the user can specify the area and the SIC code 4952, which pertains to POTWs. This will Identify each Industrial plant which discharges to each POTW, and will provide flow data. A Needs Survey data base retrieval can then be conducted for Information on treatment types employed. 141 For new "hypothetical" plants that are likely to discharge to POTWs (based on the available EGD documents on Industrial wastewater practices or other Information), the candidate POTWs can be chosen by examining both the IFD and the Needs Survey retrievals. The Needs Survey retrieval will list all of the POTWs In the area. The IFD will show which area POTWs are already receiving Industrial wastes; In the absence of better Information, assume that these plants will be able to handle the new plant's effluent as well. When conducting Needs Survey retrievals, do not forget to Include a request for Information on sludge treatment methods employed (see Step 2). Step 2 . Determine the methods of sludge treatment employed by subject POTWs. Acquisition of sludge treatment information actually constitutes part of the Stage III decision tree for POTW sludges (Section 2.2.3(2)). It Is Included here as a reminder to request sludge treatment Information when conducting a Needs Survey retrieval as directed in Step 1 above. 6.3 Estimating Releases from POTWs - Stage V Decision Tree In this stage, the user estimates releases to surface waters from POTW effluents based on knowledge of Influent concentrations and plant design/operating conditions. The output of this stage Is a compilation of releases (mass per unit time), chemical concentrations (mass per mass or mass per volume), and flow (volume per unit time) associated with aqueous discharges from POTWs. Releases to air from POTWs may also be estimated In Stage V, provided that reliable monitoring data or estimation methods are available. In order to estimate releases from land treatment, surface Impoundment, or deep-well Injection of POTW wastewaters, the user Is referred to the Stage V decision trees for those disposal methods. A detailed decision tree has not been developed for this stage, since the lack of a generally useful model precludes the accurate estimation of releases. The Stage V output should also Include estimates of the quantity of POTW sludge and of the quantity of the subject chemical In the sludge. (This Information Is Input for the estimation of environmental releases associated with disposal of the sludge, starting with Stage III.) Step 1. Identify and list the significant POTW design and operating characteristics that affect environmental releases of chemical substances. 142 The type of wastewater and sludge treatment components, and the plant design capacity In relationship to actual quantity of wastewaters treated are the key factors that determine environmental releases of chemicals from POTWs. Step 2. Determine which of the parameters listed In Step 1 are known for the slte(s) of Interest based on accessible (e.g., computerized) data. Information on wastewater and sludge treatment components and on current design and operating capacity Is available In computerized form from a Needs Survey retrieval where site-specific data Is required. For regional or large-scale exposure assessments where exposure estimates for a large geographical area (e.g. nationwide) will be based on extrapolation from one or more "typical" plants, design and operating capacity from such typical plants can be extracted from the annual Needs Survey summary (e.g., USEPA 1981e) or from a Needs Survey retrieval for the region of Interest. See Table H-8 In Appendix H for a listing of the treatment components Included in the Needs Survey and Exhibit H-l In Appendix H for a description of the scope and utility of the Needs Survey. Note that the Information required for this step should be coordinated with other Information needed from the Needs Survey so that only one retrieval Is necessary (see Sections 2.3.3(2), 2.3.3(3) and 6.2). Step 3. Identify a suitable approach for predicting environmental releases based on design/operating characteristics. The only model Identified In this study as potentially useful In estimating chemical releases from POTWs Is the POTW model developed by the Monitoring and Data Support Division (MSDS) of the EPA Office of Water Regulations and Standards (see Section 6.1.3 for a discussion of the scope and limitations of this model). The MDSD POTW model may be useful In exposure assessments of priority pollutants (or of analogous chemicals) In cases where the model POTW (based on a typical plant with secondary treatment) adequately represents the POTWs of interest In the assessment. In the case of exposure assessments for which the MDSD model Is not suitable, data allowing estimation of the partitioning of the chemical or a suitable analog among aqueous effluent, sludge, and air should be procured. The only such source of data Identified In this study is the Burns and Roe (1982) report which Is limited to priority pollutant (see Tables H-l through H-7 in Appendix H). 143 Step 4 Step 5 Step 6 Step 7 Using the available predictive approach, estimate the releases to water and to sludge of the chemical from each POTW of Interest In the assessment. (Chemical releases to air from POTWs are not usually evaluated In exposure assessments, because they are assumed to result In Insignificant exposure.) Compare estimates from Step 4 with available monitoring data, If any. If estimates and monitoring data do not agree, re-evaluate the predictive methods and repeat the analysis. If necessary. Use the estimates of sludge generated as Input to Stage III (Section 2.3.3(2)) and complete the analysis of environmental releases from disposal of the sludge. Complete the exposure assessment using Volumes 1, 2, and 5 of this methods development series. POTW effluents are usually treated as a point source In the analysis of environmental fate. 144 7. INCINERATION Incineration Is the controlled burning of wastes resulting In their thermal destruction. Toxic gases and particulates may be emitted to the air during Incineration, and Incinerator residues require ultimate disposal to land and surface water. Considerable Information Is available on the location and design of Incinerators. However, this study Identified no validated model for estimating environmental releases of a range of chemicals from Incinerators or for predicting the chemical composition of Incinerator residues. Thus, there will be considerable uncertainty In the Stage V estimates until an appropriate predictive approach Is developed. Background Information on this method Is presented In Section 7.1, followed by the Stage IV and Stage V decision trees In Sections 7.2 and 7.3. For Information on the ultimate disposal of and environmental releases from Incineration residues, see Section 2.3.3(1). 7.1 Background Information This section presents Information that Is the basis for the Stage IV and Stage V decision trees on Incineration. This Includes discussions of the types and numbers of Incinerators, Important Information resources on Incineration, emissions and by-products of Incineration, and approaches to estimating environmental releases. 7.1.1 General Incineration Is currently used as a waste treatment method for municipal sludge, municipal solid waste (MSW), and Industrial wastes (hazardous and nonhazardous). Some Incinerators are designed for some form of resource recovery, most often steam production. The advantages of Incineration as a waste treatment technique are that the waste volume Is considerably reduced and the resulting residues are largely Inert. Disadvantages Include the expensive air pollution control equipment and high energy requirements necessary for compliance with regulations Issued under the Clean Air Act and the Resource Conservation and Recovery Act (RCRA). Four classes of Incinerators have been defined for regulatory purposes: municipal, sewage sludge, Industrial, and hazardous waste Incinerators. (Hazardous waste Incinerators are actually a subset of Industrial Incinerators.) Industrial boilers sometimes burn refuse-derived fuel (RDF), which may contain toxic chemicals. However, they are not currently subject to federal regulation, and little Is known about their operating characteristics or the types of waste they burn. Industrial boilers will not be considered further In this report; however, an Inventory of municipal waste-fired boilers Is presented In 145 Appendix I, Table 1-1. Certain other methods of thermal waste treatment are not yet widely used In the U.S. and will not be discussed In this report. These Include wet air oxidation, flash drying, and pyrolysis. Each major category of Incinerators Is discussed below. (1) Municipal Incinerators . Municipal Incinerators are defined as Incinerators that burn at least 50 percent municipal solid waste. Their numbers have decreased In the last decade because of the high cost of air pollution control equipment and energy. The total national solid waste disposal capacity of Incinerators decreased by 40 percent between 1971 and 1976 (Helfand 1979a). In 1972, there were 193 Incinerator plants, and In 1977 there were only 103 Incinerator plants with 252 furnaces and a total solid waste disposal capacity of about 36,000 kkg/day. More recent surveys of municipal Incinerators are presented as Tables 1-2 and 1-3 In Appendix I of this report. These Indicate that there are currently only 90 small municipal Incinerators (capacity less than 45 kkg/day) and 46 large municipal Incinerators (capacities between 48 and 1,450 kkg/day). (Although the data do not specify whether It Is plants or furnaces that are enumerated, It Is most likely that the figures refer to plants.) Four types of furnaces are used for Incineration of MSW: vertical circular, multicell rectangular, rectangular, and rotary kiln furnaces. The rectangular furnace is the most common type (Helfand 1979a). When these furnaces are properly operated, the following temperatures are typical of various stages in the Incineration process: • Temperature of gases immediately above burning wastes: 1150°-l370°C • Temperature of gases when they leave combustion chamber: 760°-980°C • Temperature of gas entering stack: less than 540°C Municipal Incinerators are routinely operated for periods of from 8 to 24 hours a day for 5 to 7 days a week. One survey showed that 53 percent operated 24 hours a day and 36 percent operated 8 hours a day. The current trend Is toward 24-hour operation (Rubel 1974). Several kinds of emission control devices used are on municipal Incinerators. Incinerators constructed between 1955 and 1965 generally used mechanical cyclone collectors, which have particulate removal efficiencies of 60 to 80 percent. Other emission control systems Installed Included various scrubber techniques and electrostatic precipitators (ESP). (2) Sewage sludge Incinerators . Disposal of municipal wastewater treatment sludge by Incineration Is the most common method of handling these sludges (see Table 6 In Section 2.3.3(2)). Sewage sludge 146 Incinerators are defined as those that burn more than 50 percent sewage sludge (Helfand 1979b). In 1979, It was estimated that 240 municipal sewage sludge Incinerators were In operation. The majority (80 percent) of the plants have multiple hearth furnaces (MHF) which burn an estimated 85 to 90 percent of the Incineration sludge (Helfand 1979b, USEPA 1979a). Most of the remaining sewage sludge Incinerators are fluidized bed reactors (a relatively new technology). Electric (Infrared) Incinerators are even newer and are used by about nine plants (Helfand 1979b). Thirty- eight states have at least one sludge Incineration facility. Figure 1-1 In Appendix I presents the geographic distribution of sewage sludge Incinerators In 1978. Sewage sludge Incinerators generally use sludge that has at least 20 percent solids. Multiple hearth Incinerators have capacity ranging from 91 to 3600 kg/hr of dry sludge with operating temperatures ranging from 700°C to 1100°C. Gas temperatures may exceed 760°C In the combustion zone. Scrubber equipment has been the traditional air pollution control In sewage sludge Incinerators. Control technology In place today Includes Venturi scrubbers In series with cyclonic mist eliminators, Impingement type scrubbers, or multiple series of perforated plate Impingement scrubbers. No plants employed baghouse or electrostatic precipitators In 1978, but these are expected to be used In the future (Helfand 1979b). (3) Industrial Incinerators . This category of Incinerators has been defined by the EPA as any combustion unit used In the process of burning a nongaseous Industrial waste stream (Including hazardous waste) which does not recover any heat for a useful purpose (USEPA 1980d). By this definition, an Industrial waste stream means any waste stream that Is composed of more than 50 percent by weight of waste generated at a manufacturing establishment or collected by a resource recovery establishment. Industrial Incinerator designs In use Include single chamber, multiple chamber, rotary kiln, rotary hearth, multiple hearth, liquid Injection, conical, and fluidized bed units. Commercial off-site Incineration facilities generally use the rotary type and operate 24 hours per day. The total estimated population of Incinerators used by manufacturing Industries Is given In Table 1-4 In Appendix I. Table 1-5 presents an up-to-date Inventory of all hazardous waste Incinerators, a subset of Industrial Incinerators. (Because hazardous waste Incinerators are a subset of the Industrial Incinerator population, the Incinerators listed In Table 1-5 are probably also Included In Table 1-4.) Table 36 presents a list of commercial (off-site) hazardous waste Incinerators. 7.1.2 Information Resources Information on the number of Incinerators In each category comes from a variety of sources. Incinerators that are considered major sources (emitting 100 tons/year of a criteria pollutant) are listed In 147 Table 36. Commercial Off-site Hazardous Waste Disposal Facilities Offering Incineration Services in 1980 EPA Region Number of facl1Ites Amount of waste handled, thousands of wet kkg Percentage of off-site wastes handled 3 Percentage of total wastes handled 13 1 3 23 7.7 2. 1 1 1 1 26 4.0 0.83 1 1 1 1 48 7.9 1.1 IV 7 65 7.1 0.62 V 6 97 7.3 1.5 VI 6 98 9.5 0.93 VI 1 0 0 0 0 VI 1 1 0 0 0 0 IX 1 40 7.5 1.4 X 0 0 0 0 TOTAL 25 398 6.6 0.97 Percentage of all off-site handled wastes Incinerated. Percentage of all hazardous wastes generated that are handled by off-site incinerators. Source: USEPA 1980b. 148 the National Emissions Data System (NEDS) data base (see Appendices A and C of Volume 2 of this report). Hazardous waste Incinerators are entered Into the Hazardous Waste Data Management System (HWDMS) data base (see Section 2.3.3(4) and Exhibit D-l In Appendix D). Tables 1-2 through 1-5 In Appendix I present Inventories prepared by EPA. Commercial Incinerators other than those handling hazardous wastes have not been well studied and are not considered here. Information on environmental releases from Incinerators Is available from sources mentioned In Section 7.1.3, and from air data bases listed In Volume 2, Appendix A of this methods development series, 7.1.3 Emissions and Products of Incineration Incineration produces a number of by-products. Including gases and particulates (fly ash) emitted to the air, scrubber water and other wastewater, and bottom ash. The disposal methods and characteristics associated with the ash and wastewater are discussed In Section 2.3.3(1). The air releases depend on the kind of waste, the design of the Incinerator, and the pollution control equipment. The particulate matter that Is not trapped by the pollution control device becomes an air release. The following Is a summary of typical fly ash collection efficiencies of different control devices (Rubel 1974): • Settling: 0 to 31 percent • Multicyclone: 30 to 80 percent • Tangential Inlet cyclones: 30 to 70 percent • Scrubber: 80 to 95 percent • Electrostatic precipitator: 90 to 97 percent • Fabric filter: 97 to 99 percent Typical air emission factors from sewage sludge Incineration are given In Table 37. Tables 1-6 and 1-7 In Appendix I present typical emission factors from municipal and Industrial Incinerators. Tables 38 and 39 give a summary of the data collected during this study on environmental releases from municipal Incinerators. Because of the limited nature of these data, they are not necessarily typical of municipal Incinerators In general. Chemical reactions Inside Incinerators are quite complex; some organic chemical species are transformed to other species In the process. In addition, the toxic constituents In municipal solid waste vary regionally. Emission factors cannot be estimated reliably unless the toxic concentrations In the waste feed are measured. The amount of ash produced by Incineration depends on the type of waste and the type of Incinerator. Incineration of sewage sludge typically produces a residue that Is about 40 percent by dry weight of 149 Table 37. Emission Factors from Sludge Incineration ID c O to •— jQ in E •* c o — 0 (D 0 r- CD c L_ — — i • C 0 1 i j 4_ TJ r- CD 0 *o_ (D d) — JO E (D 0 4- JO — CJ) L. 3 \ E 0 4_ 0) \ Cl U i_ CD 0 (D 3 TO i_ 4- Q) 4- c — C 0 —— 0 > O E 4- — in 0 JZ 4- <0 r- CD 4- C o l i CD C mm— o — m o a. CN Q. c >* E TO ID 4- \ 8. •— CL 4_ 3 3 4— CT c 0 0 ID > 0 0 L_ —— JZ 0 •— o 4- CD -4- CO _ • 0 TO 0 1 O JZ ID •— — m in in in 0 o O —— O m in in 00 in \ T3 £ o > l \ CN \ — o • 0 JO JZ 4- (D in in in in c Q- 3 ID ** — — 0 Cl 4_ *— V* \ 1 •W > _ _ O H— 4_ _c O •— 3 (D o 0 CD CN CJ) CT ■4“ <0 'w' 0 •_ CN O 4— 4_ 0 O (D 3 4_ 'w' c 4_ 4- ID 0 a) o cz 4- JZ L. ID 4- 0 o 4- 4- o * 4- 0 • 4- i_ o Q. CL 4- L. TD H- c: E 0 E 0 0 c •— c *2 L_ 0 JO •— (D o ID o sz H— 4- T3 o C c c 0 0 0 u O O O L. —— N •— i- 0 CL mm— 4_ 0 X) ~o "O C •— T3 4~ J5 0 0 0 — 4- mm— U E (D ID 8i o — 13 0 13 0 0 c 3 — — 2 CO m CO — X Li. LU f0 JO o TJ JO CD cr> c 03 a» x 0 u u 3 o uo 150 Table 38. Summary of Total Organic Chlorine (TOCI) Inputs and Emissions at the Chicago Northwest Incinerator 3 Standard Mean deviation Refuse Input Feed rate, kg/hr 17,200 1,440 TOCI cone, ng/g 590 1,180 TOCI Input, mg/hr 9,800 18,700 Emissions Combined ash ^ Mass flow, kg/hr 4,500 800 TOCI cone., ng/g 8.1 7.6 TOCI emissions, mg/hr 35 34 Flue gas c Mass emissions, dsem/hr 86,780 6,830 TOCI cone., ng/dsem 3,200 3,500 TOCI emissions, mg/hr 285 327 Percent of TOCI emissions Combined ash 13 12 Flue gas 87 12 Overall Destruction Rate of TOCI, ?^ 97 a Thlrteen samples taken over a 13-day period. The Chicago Northwest Incinerator Is a continuously operating municipal incinerator with a furnace temperature of 1,160°F. The total weight reduction through Incineration ranges from 52 to 65?. '-’Includes bottom ash and electrostatic precipitator (ESP) ash. c Flue gas collected at the ESP outlet. ^Thls study assessed measurement errors of TOCI by adding known amounts of two surrogate compounds, dg-naphthalene and dj 2 _c h r y sene »to speci¬ mens before chemical analysis. Total percent recoveries for the surro¬ gates were low. Recoveries for dg-naphthalene were In the range of 10-50?, and recoveries for d^ 2 - chrysene were typically 30-60?. If the percent recoveries are Indicative of the recovery rate for TOCI, then TOCI concentrations are underestimated. Source: MRI 1981. 151 Table 39. Organic Compounds Quantitated in the Emission Media for the Chicago Northwest Incinerator 3 Flue gas outlet emission rate. Comb 1ned ash emission rate. mg/hr mg/hr Phenanthrene 9.2 - 28 - FIuoranthene 2.2 - 4.4 ND - 78 Pyrene 6.6 - 8.0 ND - 56 1,3-Dlch|orobenzene ND ND 1,4-DIch1orobenzene ND ND 1,2-DI chlorobenzene ND ND 1,2,3-TrIch1orobenzene 4.0 - 12 ND 1,2,4-Tr1 chiorobenzene 17 - 48 ND 1,3,5-TrIch1orobenzene 15 - 40 ND Tetrachlorobenzene 54 - 120 ND Hexach1orobenzene 4.0 - 22 ND Dlchlorophenol 22 - 54 ND TrIch1orophenol 98 - 160 ND TetrachlorophenoI 96 - 140 ND Pentach1orophenol 14 - 36 ND Dibenzofuran 5.8 - 11 ND PCBs D ImethyIphthalate D1ethyIphthalate Di-n-butyIphthalate ButyIbenzy1phthalate Bis (2-ethy1hexy1)-phthalate 1.1 - 7.8 ND - 400 ND 54 - 260 ND 420 - 3,000 3 See Table 38 for Information on this study. ND denotes that the compound was not detected. Blank denotes sampling not performed. Composite refuse extracts were not analyzed so no destruction efficiency can be determined. Source: MRI 1981. 152 the original dry weight of the sludge (Walker 1979). The typical ash content of MSW Is given In Table 13 In Section 2.3.3(6). The ash In the study reported In Table 38 was 26 percent of the waste feed by weight. 7.1.4 Estimating Emissions from Incineration No validated models that predict emissions of a variety of chemical substances from Incinerators based on waste constituents and on facility design and operating factors were Identified In this study. The quantity and composition of the by-products depend on a number of factors, Including type of waste, moisture content of waste, residence time of waste, operating temperature, degree of mixing, excess air, waste feed rate, mode of waste Input, and type of pollution control equipment. The EPA Office of Solid Waste Is currently undertaking studies that may culminate In some standard emission factors that can be used to estimate toxic emissions. Work Is also underway to characterize the operating conditions of existing hazardous waste Incinerators and to develop models for predicting mass balances for Incinerated chemical substances; this work Is being sponsored by the EPA Office of Research and Development (ORD) In Cincinnati. Meanwhile, a model that has recently been developed by ORD for determining the destruction efficiency of hazardous wastes In boilers (Wolbach 1982) Is potentially adaptable to Incinerators as well. Numerous sampling studies of Incinerator emissions are also In progress. Until there Is a suitable model, however, estimates of emissions will have to be based on evaluation of available monitoring and test burn data. A large amount of trial burn data will probably be generated as a result of recently promulgated regulations regarding the Issuance of hazardous waste Incineration permits under RCRA (USEPA 1981c, 1982b). Permit applicants must specify the waste feed mixtures they Intend to burn. The permit then specifies for each mixture a principal organic hazardous constituent (POHC) which must be destroyed or removed as required by the applicable performance standard. The applicants must conduct trial burns and submit to EPA the calculated destruction and removal efficiency (DRE) for these POHCs. They must also supply sufficient Information to determine whether the POHCs are primarily destroyed through combustion or are removed either by air pollution control equipment or by partitioning Into the bottom ash. (The applicant Is not required to provide a detailed mass balance, however.) Detailed data are also required on the average, maximum, and minimum temperatures In the combustion zone and the air feed rate. Unfortunately, while these data will be available through the various EPA regional offices, they will not be easily retrievable; plans to enter these data Into a computerized data base have been Indefinitely postponed. Meanwhile, a report summarizing most of these data Is being prepared under the sponsorship of EPA-ORD In Cincinnati. 153 Currently feasible approaches for estimating environmental releases from Incinerators are presented In the Stage V decision tree (Section 7.3). Once emission factors are known (or estimated), the dispersion of releases to the ambient air may be modeled using the procedure for point sources outlined In Volume 2 of this report. ERA has recently published a document that provides guidelines on how to model the environmental fate of environmental releases from hazardous waste Incinerators and Includes Information on suggested screening mechanisms (USEPA 1981a); this report should be consulted by users of this methods development series. 7.2 Allocating Waste Streams to Individual Incinerators - Stage IV Decision Tree The procedure for estimating the amount of a waste that Is handled at each receiving Incinerator Is presented In this section. First, the user determines what subpopulatlon of Incinerators might handle the waste. Knowledge of the waste characteristics and whether disposal will be on- or off-site Is helpful here. Then the user estimates the amount of the waste treated at each of the candidate facilities. The Information base for this decision tree Is fairly comprehensive for all but nonhazardous Industrial waste Incinerators. The Input to this stage Is the Stage III estimate of waste quantity and chemical concentration produced per unit time, and Information on the source of the waste. The output of Stage IV Is a list of candidate Incinerator sites and estimates of the quantity of the subject waste treated at each site. Step 1 . Determine whether the disposal of the subject waste will be limited to certain types of Incinerators. The output of this step will be a list of the types of Incinerators that are candidates for disposal of waste. a. Municipal solid waste . MSW Is generally burned In rectangular furnaces. Other types Include vertical circular, multicell rectangular, rectangular, and rotary kiln. b. Municipal sludge . Sewage sludge will generally be Incinerated In a multiple hearth Incinerator, although sometimes fluidized bed or electric Incinerators are used (see Section 7.1.1). c. Hazardous wastes . Check Table 1-8 In Appendix I to see whether disposal will be limited to certain types of hazardous waste Incinerators. Knowledge of the physical and chemical nature of the waste Is essential here. 154 d. Nonhazardous Industrial solid waste . Industrial waste may be burned In single-chamber, multiple-chamber, rotary kiln, rotary hearth, multiple hearth, liquid Injection, conical, and fluidized/ bed Incinerators. See Table 1-8 In Appendix I to narrow the possibilities further. Step 2 . If applicable, determine the percentage of the waste that will be disposed of on-site versus off-site. This knowledge will be useful In Identifying the population of Incinerators that Is likely to receive It (Step 3). a. Municipal solid waste . By definition, disposal of MSW occurs off-site; therefore 100 percent of the subject waste will be disposed of off-site. b. Municipal sludge . Sludge Incinerators are usually located at or near the POTW; an exception Is the case where one POTW sends sludges to another for treatment. Assume that 100 percent of the subject waste Is disposed of on-site. c. Hazardous wastes . Most hazardous wastes that are Incineration rated are treated on-site. (There are approximately 400 hazardous waste Incinerators In the U.S., only 25 of which are commercial off-site facilities, see Section 7.1.1.) For Industry-specific Incineration practices, consult Information on Incineration In Appendix C and Table 0-5 In Appendix D. d. Nonhazardous Industrial solid waste . The available Information suggests that there are few, If any, nonhazardous off-site commercial Incineration facilities. Therefore, assume that 100 percent of the subject waste will be Incinerated on-site. This assumption could be confirmed by comparing an HWDMS retrieval with a National Emissions Data System (NEDS) data base retrieval to see whether all Incinerators not In the HWDMS data base are on-site. Information on the NEDS data base Is Included In Appendix A of Volume 2 of this methods development series. Step 3 . Identify the Incinerators that are probable candidates for treatment of the waste based on Information In Steps 1 and 2 above and available Inventories (computerized or otherwise) of disposal facilities. The output of this step will be a list of all of the candidate Incinerator sites In the study area. a. Municipal solid waste . See the current Inventories of municipal Incinerators In Tables 1-2 and 1-3 In Appendix I. These Inventories give the location of each Incinerator (by city and state). Incinerators located In the study area are candidates for treatment of the subject waste. 155 b. Municipal sludge . Based on the Needs survey data base retrieval, all of the POTWs that treat sludges by Incineration In the study area will be known (see Sections 2.3.3(2) and 6, and Exhibit H-l In Appendix H). The Needs survey retrieval will also Indicate the type of Incinerator on-site. These will be the candidate facilities for treatment of the subject waste. c. Hazardous waste . The facilities In the study area that Incinerate hazardous wastes will be known from the Hazardous Waste Data Management System (HWDMS) retrieval (see Section 2.3.3(4) and Exhibit D-l In Appendix D). (Be sure to check with OSW to cull the Incorrect entries from the HWDMS retrieval before using this Information.) If the generator(s) of the subject waste have on-site Incinerators, these Incinerators are candidates for disposal. Commercial hazardous waste facilities may also be candidates If no Incinerators are on-site. Note that hard-to-treat hazardous wastes must sometimes be shipped across several states to commercial Incineration facilities. If you think that the generator of the subject waste transports the waste to a commercial facility, assume that the nearest commercial facility with an appropriate Incinerator will handle this waste. d. Nonhazardous Industrial solid waste . Assume that all generators that have Incinerators on-site are candidates for treatment of the subject waste. Note that Industrial on-site Incinerators that are not major sources will not be listed In NEDS, thus may not be Identifiable. Step 4 . Determine whether there Is Information on the capacity and current operating characteristics for the sites listed In Step 3. If so, use this Information along with available Information on the disposal practices of the generators of the waste to estimate the amount treated at each Incinerator. The output of this step will be a list of all candidate Incinerators with the estimated amount of the waste treated at each In units of mass per time. a. Municipal solid waste . The capacities of most municipal Incinerators are given In Tables 1-2 and 1-3, Appendix I. Assume that the candidate Incinerators are operating at full capacity unless there Is Information to the contrary. b. Municipal sludge . Assume that all of the subject waste generated on-site Is treated on-site. c. Hazardous wast e. The capacity of candidate Incinerators will be given In the HWDMS retrieval. Assume that all of the waste generated at a given location Is treated In the on-site 156 Incinerator (If such exists). Likewise, assume that waste from a given source that Is shipped to off-site Incinerators will be created at one commercial facility, unless the amount generated exceeds the capacity of the off-site Incinerator. d. Nonhazardous Industrial solid waste . Use the same assump¬ tions as In Step 4.c. 7.3 Estimating Emissions from Incineration - Stage V Decision Tree The goal of this stage Is to estimate and characterize releases of chemical substances to air from Incinerators. In addition, the quantities of Incinerator residues must be estimated as well as the chemical concentrations therein. First, the user Identifies the parameters that affect emissions and tries to obtain site-specific values for as many as possible. Then the user chooses an approach for estimating emissions using the available Information on the design/operating conditions of the Incinerator In conjunction with knowledge of the Influent waste. The estimates of chemicals emitted to air are Ideally used as Input to an appropriate model of environmental fate, and the estimates of the residues are used as Input In Stage III (Section 2.3.3(1)). The decision tree below provides alternate methods for estimating environmental releases from Incinerators In the absence of a validated model. However, the output of this Stage will not be very accurate until accurate emission factors and reliable models are available. Several ongoing EPA projects may provide some of the predictive capacity that Is presently lacking for estimating environmental releases from Incinerators. Step 1. Identify suitable approaches for predicting emissions based on available Input data and degree of detail and accuracy required. Relevant design and operating characteristics usually required as Input are summarized below In (a) with their expected current availability. Prediction methods are summarized In (b) with their Information requirements. a. The following design and operating characteristics slgnlfl- cantly affect the emissions from Incinerators. Numerous other factors Influence emissions, but their effects on emissions are even more difficult to describe or quantify than those listed below: • Temperature • Residence time • Excess air • Completeness of mixing 157 • Type of pollution control • Waste feed rate • Method of waste Input « Degree of atomization for liquid wastes Operation temperatures , residence time , completeness of mixing , and method of waste Input are not generally Included In currently available Inventories and data bases. NEDS and other air data bases (see Appendix A of Volume 2 of this report) contain Information on the type of pollution control at sites that are Included In the data base. Incinerator capacity or general Information on waste feed rate Is available through NEDS, HWDMS, and the various Inventories (see Table D-5 In Appendix D and Tables 1-2 and 1-3 In Appendix I). Stack parameters, exit velocity, and facility location are available In the NEDS and other air data bases for sites listed In those data bases. A report summarizing site-specific operational features of hazardous waste Incinerators Is currently being developed under EPA-ORD sponsorship; however, this report Is not currently available. Currently no available Information summarizes the site-specific data on Incinerators on a regional or local level. Some state agencies may have such Information In their files. The RCRA Part B, treatment/storage/dlsposal TSD permit applications for hazardous waste Incinerators that will be submitted to the EPA will probably Include most of these parameters, as well as trial burn data. However, this Information Is not expected to be readily accessible In the near future. b. Currently, there are no wel1-developed, validated algorithms or models for predicting emissions of chemicals from Incinerators. Gaseous and particulate emissions depend on the completeness of combustion, which Is a function of the physical and chemical characteristics of the waste In addition to design and operating conditions. The chemical processes that occur within Incinerators are not well understood; therefore, without trial burn data or monitoring data, It Is difficult to predict chemical emissions. Furthermore, the Incomplete combustion of one class of chemicals (such as chlorophenols) may lead to emissions of another class of chemical (such as dioxins). The lack of predictive capability extends to the chemical characterization of ash, scrubber water, and quench water. A model developed for EPA-ORD may be adaptable for this purpose. This model estimates the ability of an Industrial boiler to achieve a given destruction efficiency for organic wastes (Wolbach 1982). However, until this or a similar model has been validated for Incinerators, the user must have recourse to one of the following prediction methods. 158 • Use trial burn data. If available, to predict combustion efficiency for a given chemical. A summary of currently available trial burn data Is given In Table 1-9 In Appendix I. For more details on Individual trial burns see Corlnl et al. (1980). Trial burn data submitted to EPA by applicants for hazardous waste incineration permits may also be available through the appropriate EPA regional office. If data from several trial burns (with different temperatures and residence times) are available, a graph of operating conditions versus combustion efficiency can be plotted and used to roughly estimate combustion efficiency under untested operating conditions. However, there Is considerable uncertainty In this approach. Note that this approach requires at minimum a knowledge of operating temperatures and residence time. If these parameters are not known, typical operating conditions for the type of incinerator of Interest could be used as surrogate data. Some typical operating data are given In Section 7.1.1. Additional operating data are given In Table 1-12 In Appendix I. • Using available monitoring data on the chemical of Interest, compile as many of the following parameters as possible: ranges of emission factors, removal efficiencies, and measured concentrations. Tables 38 and 39 (Section 7.1) present an example of how this was done for a few chemical substances. Use these values as Indicators of the typical behavior of the chemicals for which there are data, in the absence of belter Information. For example, the destruction rate for total organic chlorine (10C1) given in Table 38 might be applied to any specific chlorinated organic (providing that one takes into account the uncertainty expressed In footnote (d) to that table). Note that the amount of ash produced can be estimated for municipal solid waste and sewage sludge (see Section 7.1.3). This approach requires data on typical design/operating conditions of the Incinerators for which there Is monitoring information. • Qualitatively compare the ease of incineration of one chemical for which there is no incineration data with another compound for which there is trial burn, test burn, or monitoring data. Because the ease of incineration is correlated with heat of combustion, chemicals can be ranked by Incinerabl1ity If their heats of combustion are known. Table I-11 in Appendix I provides the heats of combustion for hazardous wastes listed under Appendix VIII, 40 CFR Part 261. Again, this Is a very crude estimation method because the correlation between ease of incineration and heat of combustion has not been extensively tested (USEPA and MITRE 159 1983). This approach requires knowledge of the heats of combustion for the chemical of Interest and the chemical to which It will be compared. Operating temperatures and residence time are also useful In the qualitative comparison. • For hazardous wastes. In the absence of more reliable Information, assume a 99.99 percent destruction and removal efficiency for principal organic hazardous constituents (POHCs) of the waste feed, as required by RCRA regulations (USEPA 1981c). Step 2 . Using the chosen predictive method and Input data, estimate emissions from each disposal site receiving the subject waste. The output of this step will be a list of the Incinerators with an emissions estimate for each In units of mass per time. Depending on the predictive approach, the output may Include concentration and flow. Step 3 . Compare the predicted results from Step 2 to any monitoring data that may be available. If predictions do not correlate with measured values, use best judgment to evaluate the discrepancy. If applicable, calibrate the model and rerun. Then use the estimated emissions as Input In the analysis of environmental fate and pathways and the final exposure assessment, as described In Section 5.3 of Volume 2 of this report. For a complete exposure assessment of Incinerator air emissions, stack parameters, exit coordinates, and emissions may be atmospheric transport model, such concentrations of the chemical to located downwind from the release velocity, geographic used as Input parameters In an as ATM-SECPOP, to model which various receptors point may be exposed. 160 8 . DEEP-WELL INJECTION Deep-well Injection Is a waste disposal method that Involves Injecting liquid wastes Into a permeable rock layer below the surface In geologic basins which may be confined above and below by relatively Impervious rock. Improper design or operation can cause contamination of groundwater In other aquifers, resulting In human exposure to chemical substances. Background Information on this disposal method Is given In Section 8.1, followed by the Stage IV and Stage V decision trees (Sections 8.2 and 8.3). Information Is now available on the locations of Injection wells and the wastes handled by each well from the Federal Underground Injection Reporting System (FURS), a new computerized data base operated by the Office of Drinking Water at EPA. Estimating releases to groundwater from deep wells Is very difficult and subject to considerable error. 8.1 Background Information This section contains general Information on deep-well Injection, followed by discussions of (1) the Important sources of possible wastes and (2) approaches to estimating releases to groundwater. 8.1.1 General The governing principle behind deep-well Injection Is to dispose of a maximum quantity of wastes (Including those that are hard to treat, toxic, hazardous, and Innocuous) at minimum cost and Impact to the environment. Liquid wastes are usually Injected Into rock formations that are below and Isolated from fresh water aquifers. Theoretically, a properly selected reservoir can safely contain the Injected wastes, as long as the waste volume does not exceed the available volume of the reservoir and Injection pressures do not exceed critical formation pressures (Wiles 1978). However, there Is a controversy about whether It Is really possible to predict the final disposition of Injected wastes; there are numerous site-specific and general data gaps regarding saline aquifer chemistry and the chemical and micro¬ biological reactions within the receiving aquifer. Relationships between waste components, structural geology, mineralogy, and other variables that determine the persistence of Injected compounds are not well understood. Deep-well Injection Is used for a wide variety of liquid wastes ranging from domestic wastewaters and sewage sludge to hazardous and radioactive wastes. The EPA estimates that there are as many as 650,000 Injection wells In the U.S., 85 percent of which are located In the following 22 states: Arizona, Arkansas, California, Colorado, Florida, Illinois, Indiana, Iowa, Kansas, Kentucky, Louisiana, Michigan, Mississippi, New Mexico, New York, Ohio, Oklahoma, Pennsylvania, Texas, Utah, West Virginia, and Wyoming (USEPA 1981b). 161 EPA classifies Injection wells In five categories for the purpose of regulation; these categories are listed In Table 40. The classification system Is based on the zone of Injection (which depends on whether wastes are Injected above, Into, or below aquifers bearing potable water) as well as the source and type of waste. The Injection wells that are likely to be of Interest for chemicals assessed under TSCA are In Classes I and IV and constitute a very small fraction of the total population of Injection wells. (The vast majority of Industrial Injection wells are In Classes II and III, which comprise wells used In oil and gas production and mining, respectively.) A recent survey (USEPA 1980g) Indicates that only about 268 operating Industrial and municipal wells are In Classes I and IV. These are further classified as follows: II, Industrial disposal well; 1M, municipal disposal well; and 4H, hazardous facility Injection. Class 5W may also be of Interest, but Includes septic tanks and cesspools used for multiple dwellings (It does not Include single family residential waste disposal systems). A summary of Injection wells by Industry category for Classes II, 1M, and 4H Is presented as Table 41. Note that most of the wells are operated by the petrochemical, petroleum refining, and oil and gas extraction Industries. Table 41 also gives typical well depths for this group. Most of these Injection wells are on-site; only nine off-site commercial hazardous waste Injection wells were Identified In a recent EPA study, all of which are In Regions V and VI (see Table 42). Nationwide, about 2 percent of the hazardous wastes generated are disposed of by deep-well Injection (Table 42). Many kinds of wastes are suitable for deep-well Injection. Table J-l In Appendix J lists all chemicals known to have been Injected. Hazardous materials which are persistent In the environment are not recommended for this disposal method because the long storage period required to reduce the hazards to an acceptable level Increases the chances that the waste will escape as the result of system failure or migration of fluids. Chlorinated hydrocarbons are not suitable for disposal by deep-well Injection (USEPA 1980b). A recent study suggested that the following chemicals are also unacceptable for deep-well Injection (Wiles 1978): • Acrolein • Arsenic and arsenic compounds • Cadmium and cadmium compounds • Carbon disulfide • Cyanides • Dlazlnon and other pesticides o Fluorides • Hydrocyanic acid • Hydrofluoric acid • Hexavalent chromium compounds • Mercury and mercury compounds • Nltrophenol 162 Table 40. Classifications and Types of Injection Wells Well Code Class/Type Primary Function of Injection Wells Cl ass 1 Industrial, municipal, and nuclear storage wells that inject below deepest underground source of drinking water 1 l a Industrial disposal well 1M a Municipal disposal well IX Other Class t wells Class 1 1 Oil and gas production and storage-re 1ated injection wells 2A Annular injection well 2D Produced fluid disposal well 2H Liquid hydrocarbon storage well 2R Enhanced recovery injection well 2X Other Class II wells Class 1 1 1 Special process injection wells 3G In situ gasification wells 3M Solution mining well 3S Sulfur mining well by Frasch process 3U Uraniurn mining well 3X Other Class 111 welIs Class IV Hazardous facility wells that inject into or above an underground source of drinking water 4H a Hazardous facility injection Class V All other wells that Inject into or above an underground source of drinking water 5A Air conditioning/cooling water return well 5B Salinity barrier well 5D Storm water drainage well 5F Agricultural drainage well 5G Other drainage wells 5H Gaseous hydrocarbon storage wel 1 5R Recharge wel1 5S Subsidence control well 5W a Waste disposa1 well 5X Other Cl ass V wells 5N Nuclear waste disposal or storage well 5T Geothermal wel1 a Li kel y to be of most interest in exposure assessments conducted by the EPA Office of Toxic Substances. Source: EPA Form 7500-48 (11-79). 163 Table 41. Standard Industrial Classification of Injection Wells (268 Wei Is) I ndustry_No, of wells_Percentage MINING (9.3%) 10 Metal mining 2 0.7 12 Coal 1 0.4 13 Oil and gas extraction 17 6.4 14 Non-metal 1ic mining 5 1.9 MANUFACTURING (80.6$) 20 Food 6 2.2 26 Paper 3 1.1 28 Chemical and allied products 131 48.9 29 Petroleum refining 51 19 32 Stone and concrete 1 0.4 33 Primary metals 16 5.9 34 Fabricated metals 3 1.1 35 Machinery - except electronics 1 0.4 38 Photographics 3 1.1 TRANSPORTATION, GAS, and SANITARY SERVICES (9.8?) 47 Transportation service 1 0.4 49 Sanitary service 23 8.6 50 Wholesale trade - durable 1 0.4 55 Auto dealers and service 1 0.4 OTHER (0.4?) 72 Personal service 1 0.4 WELL COMPLETION DEPTHS (262 Wei Is) Depth 3 No. of wells Percentage 0 - 1,000 20 7.6 1,001 - 2,000 56 21.4 2,001 - 3,000 33 12.6 3,001 - 4,000 34 12.8 4,001 - 5,000 39 14.8 5,001 - 6,000 44 16.7 6,001 - 7,000 18 7.2 7,001 - 8,000 12 4.8 8,001 + 3 1.2 g i ven in source. but they are probably feet. Source: USEPA 1980g. 164 Table 42. Commercial Off-site Hazardous Waste Disposal Facilities Offering Deep-wel1 Injection Services in 1980 by EPA Region Amount of No. of waste hand 1ed (thousands of Percentage of off-site Percentage of total EPA Region faci1ities wet kkq) waste handled 3 waste handled* 3 1 0 0 0 0 1 I 0 0 0 0 1 1 1 0 0 0 0 IV 0 0 0 0 V 1 152 11.4 2.3 VI 8 635 61.7 6.0 VI 1 0 0 0 0 VIII 0 0 0 0 IX 0 0 0 0 X 0 0 0 0 TOTAL 9 788 13.0 1.9 Percentage of ^Percentage of total off-site handled total waste generated waste treated in region that by deep-wel1 injection, is disposed of at off-site I nject ion wells- Source: USEPA 1980b. 165 8.1.2 Information Resources Useful In Assessing the Potential for Exposure from Injection Wells Injection wells will be closely regulated under new federal and state regulations. EPA Is requiring the states to develop programs to prevent contamination of groundwater by Injection wells for the Underground Injection Control (UIC) program brought about by the Safe Drinking Water Act. As a result of the concern over the potential for groundwater contamination from Injection wells, there Is considerable site-specific Information on existing wells. Under the UIC program, a new computerized data base Is available to keep track of Injection wells. This data base Is called the Federal Underground Injection Reporting System (FURS) and contains data on Injection wells In the U. S. This data base lists all wells and Includes Information on the location, operational status, and well class for states that do not have an approved UIC program. Because the class Is somewhat Indicative of the types of waste that It receives (see Table 40), this Inventory will be useful In exposure assessments. Also, Region VI already has Its own computerized Injection well data base, which contains detailed site-specific data. Until the UIC program Is fully operative, hazardous waste Injection wells (Class IV) will have to submit RCRA permit applications. Therefore, the Hazardous Waste Data Management System (HWDMS) (see Section 2.3.3(4) and Exhibit D-l In Appendix D) contains Information on the location, SIC Code, and proposed capacity for hazardous waste Injection wells. State agencies are currently the best source of site-specific geological, hydrological, and design data for Injection wells not located In Region VI. These data will generally have to be retrieved manually. 8.1.3 Modeling Releases to Groundwater See Section 3.1.3 for a general discussion of modeling groundwater contaminated from waste disposal sites and Volume 5 of this methods development series for more Information on groundwater modeling. The modeling of groundwater contamination via deep-well Injection Is even more difficult than for previously mentioned land disposal methods because of the considerable difficulty and expense Involved with obtaining Information to run such models. As In most cases Involving groundwater models, the assistance of a hydrogeologist will be required. Should accurate and concise Information be a necessity, then the assistance of a company such as GeoTrans Inc., Reston, Virginia, which specializes In groundwater studies, may be required. The EPA has developed an approach to regulating Injection wells that has the potential to serve as a coarse screening tool In determining which wells may present the greatest risk of groundwater contamination. The regulations prescribe that a "zone of endangerment" be designated for each Injection well. Zone of endangerment Is defined as the theoretical circular area (centered on the well) In which the pressures In the Injection zone may cause 166 the migration of the Injection and formation fluid Into an underground source of drinking water (USEPA 1981d). If this radius could be accurately determined for any Injection well (which Is questionable), then the potential for contamination of groundwater supplies could be estimated qualitatively. A modified This Equation that can be used to calculate the zone of endangerment Is given as Table J-2 In Appendix J. Computation of the zone of endangering Influence requires the following parameters: • Hydraulic conductivity of the Injection zone (length/time) • Thickness of the Injection zone (length) • Time of Injection (duration/time) • Storage coefficient (dimensionless) • Injection rate (volume/time) • Observed original hydrostatic head of Injection zone (length), measured from the base of the lowest Underground Source of Drinking Water (USDW) • Hydrostatic head of the USDW (length), measured from the base of the lowest USDW • Specific gravity of the fluid In the Injection zone (dimensionless) These parameters are representative of the parameters commonly used In groundwater modeling. When considering whether to Issue a permit to an applicant, EPA or the responsible state agency will review available site-specific data on the number and location of all wells, surface waters, springs, mines, quarries, location of USDWs, residences, roads, and geology In the zone of endangerment. These same parameters, which will be available In agency files, should be considered when the potential for exposure from a given Injection well Is assessed, because the primary route of exposure will be via drinking or other contact with water from USDWs. Determining the appropriate groundwater models for site-specific estimates of emissions from Injection wells Is beyond the scope of this methodology and will best be left to the modelers. Good sources of Information on the multitude of available groundwater models Include the EPA Ground Water Models Clearinghouse, a computerized data base that provides summaries of the Important features of 300 models (see Appendix A) and a groundwater model review report by the EPA Office of Solid Waste (USEPA 1982a). See Section 8.3 for Information on a model that has been used to approximate pollutant migration from Injection wells. 8.2 Allocating Waste Streams to Individual Injection Wells - Stage IV Decision Tree In this stage, the available Information on the locations of Injection wells of the class appropriate for the waste stream of Interest will be reviewed, In order to select the Individual wells likely to receive the waste stream of Interest. Then the amount of the waste stream of Interest disposed of In each candidate well will be determined. The body of Information upon which these decisions are made Is extensive. 167 Step 1 . Determine whether disposal of the waste will be limited to certain classes of Injection wells. The output of this step will be a list of the relevant classes. Consider the characteristics of the waste and Its origin. The classification and type of Injection well receiving the waste will depend on the nature and source of the waste. Consult Table 40 to determine the class of well appropriate for disposal of the waste. If there Is uncertainty over which type of well Is appropriate, consult USEPA 1981d for a more complete description of the well classification system. Step 2 . If applicable, determine the percentage of the waste that will be disposed of on-site versus off-site. The output of this step will be the list of well classes compiled In Step 1 to which the percentage of on-site versus off-site disposal has been added for each well class. This Information will be useful In Identifying wells that are candidates for disposal of the waste (Step 3). Municipal disposal wells will be, by definition, off-site, but are probably located at or near a treatment works POTW. Waste disposal Injection wells will also be off-site, since they are usually the repository for wastewaters from multiple dwellings. Most Industrial Injection wells are on-site. The only off-site commercial facilities known to exist are those few that handle hazardous wastes (see Table 42). For site-specific Information on whether disposal will be off-site, conduct a retrieval of the (FURS) and see whether any of the generators of the waste stream of Interest have Injection wells on-site. Supplement this with a Hazardous Waste Data Management System (HWDMS) retrieval (see Section 2.3.3(4) and Exhibit D-l In Appendix D). If the Information from these two sources Is Insufficient, contact the agencies responsible for the Underground Injection Control program (UIC) In the state(s) of Interest. Assume that all generators with on-site wells that are classified appropriately will dispose of the waste on-site If It Is suitable for Injection (see Section 8.1). Otherwise, use best judgment to determine whether the waste might be disposed of In off-site Injection wells, based on knowledge of the waste disposal practices of the Industry for similar wastes. Note that some generators of d1ff1cult-to-treat hazardous wastes have to ship them across the U.S. for disposal In commercial Injection wells. One novel use of the HWDMS In this regard would be to conduct a retrieval of all hazardous waste Injection wells, requesting the auxiliary data on waste codes treated. Even though these data are considered unreliable for quantitative purposes (see Section 2.3.3(4)), they will provide general Information on the kinds of wastes that a given facility might accept for deep-well Injection. 168 Step 3 . Based on the Information In Steps 1 and 2, and available Inventories (computerized or other) of disposal facilities, Identify the Injection wells that are candidates for the disposal of the waste. The output of this step will be a list of the candidate Injection wells. The FURS retrieval combined with the HWDMS retrieval and Information from state agencies will provide a list of all on-site Injection wells. The Needs survey data base retrieval (see Sections 2.3.3(3) and 6, and Exhibit H-l and Table A-8 In Appendix H) will Indicate which POTWs use this disposal method. Assume that all generators with on-site wells of the appropriate class will dispose of the waste on-site. Consider the discussion In Step 2 In deciding which off-site wells may receive the waste. Step 4 . Determine whether there Is Information on the capacity and current operating characteristics for the candidate sites listed In Step 3. Use this and any other relevant Information to estimate the amount of the waste that will be disposed of at each facility In units of mass/time. The output of Stage IV will be the Step 3 list to which individual amounts of dlsposed-of waste have been added for each Injection well. Assume that all of the waste generated at a given source will be disposed of In one Injection well, unless It exceeds the capacity of the well. Capacities of hazardous waste Injection wells will be given In the HWDMS retrieval. Additional Information on capacity may be available from the state agencies In charge of the UIC program. 8.3 Estimating Releases from Injection Wells - Stage V Decision Tree This decision tree presents the available approaches to estimating the releases of the chemical substance to groundwater from deep-well Injection. As stated previously, the modeling of contamlnent migration from Injection wells Is very difficult and probably best performed by hydrogeologists. Many variables that affect the contamination potential are either little under¬ stood or difficult to quantify on a site-specific basis. Step 1 . a. Identify the Important design and operating characteristics of Injection wells that affect releases to groundwater. See Section 8.1.3 for the list of parameters that govern thephyslcal behavior of Injected fluids. In addition to these factors, the type of casing and cementing used In constructing the well Is critical because It must prevent the movement of fluids Into or between other sources of drinking water. Therefore, It must be able to withstand all of the normal stresses associated with use, Including Injection pressures, corrosiveness of Injected fluid, and fluctuating temperatures. 169 b. Determine which of the parameters listed In l.a are known for the sites of Interest based on accessible computerized data or other readily available data. Information on most of the parameters discussed In Step l.a will be available In the application submitted to the EPA (or to the responsible state office) after the UIC program Is operable, but Is not generally available In computerized form at this time. The EPA Region VI data base probably contains most of the Important data already. c. Identify which of the parameters listed In l.a can be obtained from existing files at regional EPA offices and responsible state solid waste agencies when not available from the sources listed In 1 .b. Many state agencies responsible for permitting Injection wells, especially those states that have numerous Injection wells, will probably have most of these data In their files. Some of these data have also been collected for Industrial wells In EPA surveys (see Reeder et al. 1977b) and can be obtained from such reports. Step 2 . a. Identify and list the approaches that are available for predicting environmental releases based on the design/operating characteristics of the wells. As discussed In Sections 3.1.3 and 8.1.3, numerous groundwater models have been developed. The Land Disposal Division of the EPA Office of Solid Waste Is developing a set of test problems for evaluating new mathematical models of saturated zone leachate migration with respect to their utility In predicting pollution migration from land disposal and Injection wells. They have used a model program called SWIP (Survey Waste Injection Program) developed by US6S (Mercer et al. 1981). This model was developed to Investigate problems associated with the disposal of wastes In deep wells and Is applicable for modeling the transport of momentum, energy, and contaminant mass In porous media associated with deep-well Injection or other sources. Appendix J-3 presents a summary of this model. While other models may also be applicable for use In Injection wells, this model Is used here as an example of the Input requirements. Modeling of deep wells Is highly complex, and model selection Is beyond the scope of this methodology. b. Identify the site-specific design/operating characteristics required for Input by the model of choice. Determine whether these data are readily available. If not, determine whether there are surrogate values that can be used In place of the site-specific parameters. 170 As an example of the data elements that may be required, the following list gives Input parameters that are used for various solutions available using SWIP: • Aquifer thickness (length) • Aquifer compressibility (assumed 0.0/psl In one test problem) • Porosity (unitless) • Water unit weight (62.4 1b/ft3) • Water compressibility (0.00115/ps1) • Hydraulic conductivity (length/time) • Initial pressure (ps1) • Wellbore radius (length) • Reservoir exterior radius (length) • Effective molecular dlffuslvlty (area/time) • Velocity (length/time) The parameters needed In SWIP will generally be available In standard references and state and EPA files once the UIC Is operable; many state agencies may already collect the requisite Information. Because of the highly site-specific nature of groundwater hydrology, It Is generally thought that the magnitude of error Introduced by attempting to use surrogate data renders predictions based on surrogate data of little use. (Even with accurate site-specific data, groundwater models make simplifying assumptions that may not be warranted.) Note that this model does not describe biological or chemical processes associated with deep-well disposal. Step 3 . Input the data Into the chosen model and run the model to produce an evaluation of chemical releases. If an appropriate model Is applied correctly and accurate site-specific data are available, the groundwater model can provide various types of output data, the most Important of which are contaminant concentrations that may lead to or be a drinking water source. Step 4 . If monitoring data are available, compare them with the model predictions to test the accuracy of the model application. 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U.S. Environmental Protection Agency. Office of Solid Waste and Emergency Response. Lining of waste Impoundment and disposal facilities. Washington, DC: U.S. Environmental Protection Agency. SW-870. USEPA and MITRE. 1983. Guidance manual for hazardous waste Incinerator permits. Washington, DC: U.S. Environmental Protection Agency. Office of Solid Waste (Note: report scheduled to be published In August 1983.) 178 Van Noordwyk HJ. 1980. Quantification of municipal disposal methods for Industrially generated hazardous wastes. In: USEPA. Treatment of hazardous waste. Proc. 6th annual research symposium. Cincinnati, OH: U.S. Environmental Protection Agency. EPA-600/9-80-011. Versar Inc. 1983. Theoretical evaluation of sites located In the zone of saturation. Draft final report. Chicago, IL: U.S. Environmental Protection Agency. Contract No. 68-01-6438. Wagner J, Bonazountas M. 1981. Burled halogenated solvent simulations via "SESOIL." Draft report. Washington, DC: U.S. Environmental Protection Agency. Contract No. 68-01-6271. Walker JM. 1979. Overview: costs, benefits and problems of utilization of sludges. Proceedings 8th National Conference on Municipal Sludge Management, Information Transfer. Silver Spring, MD. Wetherold RG, Rosebrook DD, Cunningham EW. 1981. Assessment of hydrocarbon emissions from land treatment of oily sludge. In: USEPA. Land disposal: hazardous waste. Proc. 7th annual research symposium. Cincinnati, OH: Municipal Environmental Research Laboratory, U.S. Environmental Protection Agency. EPA-600/9-81-002b. Wlgh RJ, Brunner DR. 1979. Leachate production from landfilled municipal waste - Boone County field site. In: USEPA. Municipal solid waste: land disposal. Proc. 5th annual research symposium. Cincinnati, OH: U.S. Environmental Protection Agency. EPA-600/9-79-023a. Wiles CW. 1978. Assessment of deep well injection of hazardous waste. In: USEPA. Land disposal of hazardous wastes. Proc. 4th annual research symposium. Cincinnati, OH: Municipal Environmental Research Laboratory, U.S. Environmental Protection Agency. EPA-600/9-78-016. Wolbach CD. 1982. Prediction of destruction efficiencies. Environmental Progress 1(1):38-41. Yeh GT. 1981. AT123D: Analytical transient one-, two-, and three-dimensional simulation of waste transport In the aquifer system. Oak Ridge, TN: Oak Ridge National Laboratory, Environmental Sciences Division Publication No. 1439. 0RNL-5601. 179 APPENDICES GUIDE TO APPENDICES These appendices provide Information Intended to supplement "Methods for Assessing Exposures from Disposal of Chemical Substances," Volume 3 of the series "Methods for Assessing Exposures to Chemical Substances." The format herein Is organized Into eleven appendices (Appendices A through K) based on subject matter. The appendices comprise a wide range of Information resources Including lists of useful contacts at state and federal agencies, sample data on waste generation rates and quantities of wastes handled by various disposal practices, sample Inventories of existing disposal facilities, generic data on design and operation of disposal facilities, data on emission factors, and Information on useful data bases and models. The appendices assembled herein are Intended to acquaint the user with key Information resources that may be useful In assessing exposures to chemicals resulting from disposal. They are not meant to be the sole or even the major Information resource for such exposure assessments; the body of Information of potential use In assessing exposures from disposal Is far too large and varied to Include here. Rather, these appendices should be used to supplement the Information resources described In the main text when Information needed for a given exposure assessment Is needed. Many of the sample tables Included In the appendices were reproduced from the original source with little or no modification so that the user might become familiar with the content, presentation, and limitations of available information resources. In many cases, the user will have to consult the original source to Interpret or expand upon the data given in the appendices. A description of the kind of information provided in each appendix is provided below. Appendix A . This appendix summarizes the models and data bases that are discussed In the methodology. The data bases are expected to be Important tools In evaluating exposure from disposal of chemical substances. Because the state of the art In model development does not generally meet the predictive needs of this methodology, the models In Appendix A are not necessarily suitable for exposure assessment at the present time. 183 Appendix B . This appendix (Tables B-l and B-2) Is a summary of published Information on waste generation collected from selected state solid waste agencies In the course of developing these methods. Although these reports were only collected from a sampling of states, they are expected to be representative of the kinds of Information available from all states. As might be expected, the amount of Information maintained by state solid waste agencies varies markedly. Depending on the state, Information on one or more of the following topics may be available: • Locations of disposal sites • Kinds and quantities of wastes accepted • Types and quantities of Industrial wastes generated • Information on on- versus off-site disposal • Analyses of Industrial waste streams. Thus, state solid waste agencies may provide useful generic and/or site-specific data for assessing environmental releases from disposal, particularly for Stages II, III, and IV. See Table D-3 for a list of the state solid waste agencies. Appendix C . This appendix Is a collection of compiled data on waste generation and disposal In the chemical manufacturing and petroleum refining Industries. Table C-l presents a summary of the total quantities of hazardous waste generated and the quantities disposed of off-site for the plastics, Industrial organic chemicals, petroleum refining, and petroleum re-refining Industries. This table Is followed by more detailed Information on these Industries, Including typical waste constituents, and quantities of wastes handled by various disposal practices. These tables provide generic Industry-specific data that are useful In estimating overall waste quantities (Stages I and II), and likely disposal methods (Stage III) for Industrial solid wastes. In addition, these generic data can be helpful In allocating quantities of waste to Individual disposal sites (Stage IV). For Instance, If Appendix C Indicates that the Industry of Interest generally uses on-site landfills, we can assume that all solid waste generated on-site Is disposed of In on-site landfills and allocate waste quantities accordingly. The user should be aware of the following when using Appendix C: (1) Although the Information In these reports Is generally the most comprehensive published material available, the data may not represent the current waste disposal "picture." 184 (2) Information similar to the data In Appendix C Is available for all Industries listed In Table 9 of this report. Appendix D . This appendix Is a collection of Information from sources that are useful In determining the likely disposal methods for a given type of waste containing chemical substances (Stage III). It should be stressed, however, that useful Information sources for Stage III will also be found In the other appendices. Exhibit D-l summarizes pertinent features of the Hazardous Waste Data Management System (HWDMS) data base, which provides useful Input to Stage III and Stage IV procedures for hazardous wastes. Tables D-l and D-2 provide useful generic data for determining how much wastewater will be treated by POTWs. Table D-3 Is a list of appropriate state solid waste agencies which should be consulted for state-specific waste disposal Information. Table D-4 gives the treatment/storage/dlsposal codes used In the Hazardous Waste Data Management System (HWDMS) data base; an HWDMS retrieval may be an Important source of Stage III Information. Table D-5 Is a summary of typical disposal practices for most of the Individual hazardous waste listed under RCRA. Table D-6 provides Information useful In determining whether a given hazardous waste Is likely to be Incinerated and In determining Incinerator types. Table D-7 summarizes selected HWDMS data on the disposal of hazardous waste. Finally, D-8 lists the Industries subject to effluent guidelines and pretreatment standards. Knowledge of pretreatment standards may be useful when estimating the contribution of toxic chemicals to POTWs from Industries. Appendix E . This appendix Is a collection of data related to waste disposal In landfills and by land treatment, which will be useful In Stages IV and V and for modifying first-cut Stage III estimates. Table E-l Is a summary of the U.S. population distribution In relation to wetlands (environmentally sensitive areas). This Information could be used In the absence of better data to roughly estimate the proportion of landfill acreage located In areas with high water tables on a statewide or nationwide basis. (This would be useful Stage V Information for the modeling of emissions from landfills In large-scale exposure assessments.) Table E-2 presents Information on the relative distribution of landfills of varying capacities as well as Information on the number of landfills with National Pollution Discharge Elimination System (NPDES) permits by state. Table E-3 Is a summary of the Input data requirements for the SESOIL model. Tables E-4 and E-5 summarize the geographic distribution and Industrial classification, respectively, of hazardous waste land treatment facilities Identified In a recent survey. These data, together with the map of land treatment facilities provided In Figure E-l, are essential Input to Stage IV and Stage V procedures for land treatment facilities. Figure E-2 Is a bar graph summary of the size distribution of land treatment facilities that can be used to extrapolate generic data on land treatment capacity when site-specific data are either not available or not required. 185 Appendix F . This appendix presents auxiliary Information on groundwater that may be useful In the Stage V modeling of chemical releases from landfills, land treatment sites, surface Impoundments, and Injection wells. Table F-l Is a list of computerized groundwater data bases that provide Information on depth of water table for various areas of the U.S. Table F-2 Is a list of state groundwater geologists, who are useful contacts when detailed Information on groundwater Is required for modeling purposes. Figure F-l provides a gross picture of the distribution of wetlands nationwide. In the absence of better Information, this map may serve as a source of very general Information on relative depths of groundwater. Appendix G . This appendix provides Information on surface Impoundments useful In Stage V. Tables 6-1 and G-2 give the relation between characteristics of the saturated and unsaturated soil zones beneath surface Impoundments and the SIA (Surface Impoundment Assessment) rating system. This Information will be useful If a SIA data base retrieval Is conducted to obtain data necessary for modeling. Appendix H . Appendix H Is a compilation of Information on POTWs that may be helpful In predicting emissions of chemical substances In the absence of a suitable POTW model. Exhibits H-l and H-2 provide summary descriptions of the Needs Survey and IFD data bases, both of which may be useful In estimating chemical releases from POTWs. Tables H-l through H-7 summarize the data on priority pollutants In POTW waste streams from the most comprehensive study available (Burns and Roe 1982). Tables H-l through H-4 give the results of sampling data for priority pollutants at representative secondary POTWs; the media sampled Include POTW Influent, secondary effluent, and raw sludge. Tables H-5 and H-6 summarize the treatment efficiencies of priority pollutants by the secondary treatment method. Table H-7 provides data on typical concentrations of priority pollutants In POTW sludge when not detected In Influent (which gives some Indication of the tendency of pollutants to be concentrated In sludge). Table H-8 lists the wastewater and sludge treatment methods that are Included In the Needs Survey data base; this Information will be useful In designing a Needs Survey retrieval for Stages III through V. Appendix I . A considerable body of data on Incineration Is represented In this appendix, which will be useful In Stages III through V. Figure 1-1 and Tables 1-1 through 1-5 provide Information on numbers and/or locations of various types of Incinerators In the U.S. Tables 1-6, 1-7, 1-9, I-10, 1-13, and 1-14 give data on air releases for selected chemicals that exemplify the kind of data that will be useful In the absence of a suitable model for predicting emissions from Incineration. Table 1-8 rates the Incineration potential of RCRA-llsted 186 hazardous wastes and gives the suitable Incinerator types for each waste; this Information will be useful In Stage III and In Stage IV. Table I-11 lists the heats of combustion for RCRA-llsted hazardous constituents; these data can be used In "gross" Stage V emissions estimates, as discussed In Section 7.3. Table 1-12 presents the typical operating ranges (which may be needed In Stage V models) for various types of hazardous waste Incinerators. Appendix J . Some Information on waste disposal by deep-well Injection Is compiled In Appendix J. Table J-l lists compounds that are known to have been disposed on In Injection wells; this Information may be useful In Stage III determinations. Table J-2 presents the modified Thels equation, which may be useful In Stage V estimates. Finally, Table J-3 gives a summary of the SWIP model. Appendix K . A list of conversion factors that may be useful In conducting the procedures recommended In this volume Is presented In Appendix K. 187 APPENDIX A INFORMATION RESOURCE MATRIX: MODELS AND DATA BASES USEFUL 189 ro to 03 to 03 00 03 4-> & TD C 03 03 X £ 03 to >- CD O O X O X u > 03 CD 2 I > X m 03 03 a c o > 03 U 03 C 0» U »—• c 3 2 > < (jO o 0- tO -«-> > 03 a; u X C > 03 ►—i *— > X C 03 > oj Q3 >—I 03 i—* 03 O C CO X o 03 c O L. V < o CO CM 191 t/3 cr 3 . 03 r— x c < t- o O 03 Q3 4-> c X 03 to X r— <4- U 03 • r~ c X .1— 3 03 03 X x CM u 03 o . r— TD L- 4-> uo h— 00 tf- 0) r-» X CD C to N c CM 03 X O 4-> O' CL r— CD c 03 o 00 • • *— CM 03 p— \ CM TD Ql a U u f\l 03 CM C\J 00 03 3 03 C 5- • r- 00 r— 00 00 03 O* u < C 03 03 1/1 U- u 03 r— O' c • p— 03 Q o 1 03 U. o X r— CO 03 <4- c C/> f— CO U X O u 03 JS (/» «4- • r- X 03 00 03 03 03 03 r— 03 X 03 O -X \ X CM • r— X < c X c c O) c (jO 1 L- O Q- 03 03 X 03 X 03 < • r* CD e r*** U 00 LU 5 O 03 3 C -X a. S_ t/3 o i — 03 03 2 >• X 03 C/3 LU o X CO CL '— c 03 to O u L. • p - c c t/3 03 to 4-> to to o to r— r— c c 03 X C73 to p— 03 • r- CD 03 i -*-> 03 4-> C C r— 4-» tl 03 TD o TD E to TD c — J 13 .f— ^—s 03 03 o TD Q X Q to 03 03 Q Of *-4 o 4J 03 03 X Z3 <4— Q fc= E c Q 3 X g E LL. &. 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CO cj > CD CD 5 1 :> Cl >—« o & c o -*-» > 03 u o c •r- > CJ C 3 £ => c £ 4-» 03 CD TD C 03 <— > TD C 03 > CD Q) >—• 03 *-h 00 c &.S* t/3 (D QC o u < CD U CJ u c T3 L. U S L. 03 CD • r— CD CD l/> c 00 CD L- 4-> U o CO *0 • r— < cn c 3 o • r— 3 *o 03 QC CD 0) C • r - 4-> C L. 4-> c- *4- 03 c- C 00 L- 03 L- 03 L- \ c O o o c T3 O L. O O CD o 00 03 U CD CD 4-> T3 U CJ (D CD c CD •— 03 CD <§■ CD C rg 03 • r— u CJ O oo U CL U CJ CO CJ 00 CJ u- L- . r— • r— • r- “O C 4 o> • r* p a> • r- u- o c- c- 4-> u c- >> 03 L- p L- vD (/> C4- O L- c- 03 03 w- 4-> 4-» V*- L- u 4-> L- O 3 c r— co a. o P Q_ CL < 00 < O) 03 < 03 “D < o LU < L_ L LU < LU cl 03 Q_ CD CL 3 C Q_ u CO Q- C CD CO CL LU 3t LU CL CO LU O' 03 LU CL Z) LU LU CL Z> LU 03 03 CD • r~ -*-> 4^ C/> r— 03 03 -♦-> 03 00 /—N 4 p— c Q £ • r— JO c 03 03 jQ o u3 r— o CD U 00 03 rsi CD -U • r- 03 4 r— > c 03 4 r— 4J oo u •u 00 L- 03 _Q __J 4-> CO >> 03 03 oo ZD Q 3 CO LL ■o • r- CO r— 03 O v—^ ,§ 1 X—S Q. 4-> 1 - CL u 03 *— 00 03 E 03 3 TD c OO 03 03 4-» ■o oo O “O oo C 03 ZD ' 03 4 r— C7) r— oo 03 03 O O ZD -O -8 JO S- U 03 >» 03 JO LL • r* ’I 4-» 03 c CO z 4-* E O u i— a) 03 l/> -C O 03 • r - & l 4-» <>— 03 03 ■*-> CJ 03 o E 4-» 4-» oo 4-> N c 03 -O c/> 4-* 4-> CD 03 C 00 oo 3 oo 03 £ TD c . r— 03 03 O' *o 03 >> O u 03 X 1—4 Q Z O s —' CL CO Q_ CL CO Q t/> •O i CO 192 £ a; CJ o *QJ —J o & o o I 8 C ►— O LLl 4-> rO z: U o & O QJ X U rO t— L_ > i_ HH UJ O C/0 X —1 4-> c < g CO -*-> > ro O OJ J- CL +> CO ■o c > ro HH —J o »— r— > • r“ z u- T? < C ro > > _J l-H UJ QJ _J 05 *—» rO >—* UJ 4-> ►-H CO DC QJ (J C QJ t- r— V4- u jQ QJ rO •r— U 4-> CO c 1/5 <4- Qj *4— a: o $ c O u u o c O L- (J < -O CVJ GO O' CO u QJ OJ C 05 c CO o CO .o qj co -*-> c rO o cr — 4-> QJ d 3 CO *— rO •*- aj q. 'a) o CL O 00 O' ro 4-> 05 CD J* U • r~ u CL X O qj u < CL *o C rO ro *D — C 00 4-> fO O' qj •— u c c o rO O 4-> M CO fO jQ D co co u 0) CO C ro C75 4-> • N r- ro CO C O' O •— CO o co 05 c c u Q 00 05 < QJ CL O UJ CO CO O' < CL U < a» a. CO 3 — ro O CO 4-> QJ V4- O *- 0) 0) U L) U Z £ C- \ o a; 4-> »— < CO co CL ro O' LJ 3 - c o 193 CO < < CO u 0) QJ QJ TD 4-J Q C/5 £ a; u > 05 U o o u CO CL C (/> Q • r— P JZ l7i 4-> CO QJ u- co O co ro CNJ QJ fli U c O 5 co O o Ql > X QJ QJ QJ QJ C/5 JZ 4-> . c r— •r* rO CO co 8. Ql QJ CO 4-> • r- co ■O 4-> QJ c 4-» QJ co O rO CT 2 QJ co e -Q o O u co c- “O 4-> c c rO p CO • r“ o t/5 L >> • r— > rO c C QJ rO QJ QJ 4-> 4-> rO U- O +-> *o C co rO QJ co co ro >> QJ ro r— QJ -C U 4-> rO 05 Q. c • r“ 4-> rO ffl 4-» C Q 4-> P QJ o O u 4~> > 05 c C QJ • r- *o QJ rO JC CD 4-> * c CO • r— Ql OJ 4-> z> CO u- QJ c co • r- Z3 __ co ZJ QJ u- co QJ rO co -Q ZJ ro CO 4-> QJ rO co ■o rO jQ -u C rO •o 4-> ro co “O r— QJ *o *o C Q rO E L. QJ 4-> fO C D o s. 05 c o 3 CO CD X> ■o aj u o Ql CD U CO 00 O' i_ rO CO L. QJ > TJ CD 4-> o JO c See Table F-l in Appendix F for a list of these data bases. APPENDIX B SUMMARY OF INFORMATION COLLECTED FROM STATE SOLID WASTE AGENCIES 195 Exhibit B-1. Selected Reports on Waste Generation and Disposal Prepared by State Solid Waste Agencies* The Illinois Environmental Protection Agency distributes a report entitled the "Illinois Industrial Waste Survey" (1980) summarizing the results of a multivolume study. The report summarizes quantities of waste types generated by each SIC group In the state, the percent distribution of waste types to different disposal methods (on-site and off-site), and other data. The Michigan Energy Administration, Department of Commerce, distributes four reports analyzing waste stream composition and quantities received by municipal landfills In different regions of the state. Total quantities and per capita estimates are provided. The Kansas Department of Health and Environment distributes a report entitled "A Survey of Hazardous Waste Generation and Disposal Practices In Kansas" (two volumes plus summary), listing the waste types for each Industry and quantities disposed of by each method. The Delaware River Basin Commission (West Trenton, N.J.) distributes a summary report of their "Industrial Exotic Waste Program Findings, Conclusions, and Recommendations" (1979), analyzing Industrial waste streams and disposal practices In New Jersey. The report Includes a list of all facilities In the area known to accept Industrial waste. *Th1s list Is based on a limited sampling of state solid waste agencies. This Information Is provided In order to acquaint the user with the kind of Information sometimes available on the state level. 197 Exhibit B-2. State Inventories of Disposal Facilities* The California State Solid Waste Management Board maintains a computerized data retrieval system whereby one may determine types and volumes of waste disposed, site-specific operational characteristics of facilities, and their names and locations. Use of this data base should supply most of the data requirements for the methodology for any site In California. The Missouri Department of Natural Resources distributes a report entitled "Facilities for Solid Waste Disposal and Processing" listing contacts In state regional offices, names and locations of all permitted sanitary landfills, processing facilities and transfer stations for resource recovery, and permitted special waste disposal facilities. This state also distributes "Facilities Available to Missouri Industry for Hazardous Waste Management", listing hazardous waste landfills. Incinerators, treatment, and recycling facilities. The Kansas Department of Health and Environment distributes a "Directory of Sanitary Landfills, Solid Waste Transfer Stations, and Collectors In Kansas." The May, 1981 Issue not only lists names and locations of all permitted facilities but also total quantity of solid waste received by each facility for 1978, 1979, and 1980. Kansas also distributes "A Survey of Resource Recovery Markets and Hazardous Waste Management Facilities" listing names and locations of each such facility In the state, 23 waste exchanges throughout the country, addresses and phone numbers of solid waste agencies for all states, trade associations and other sources of Information and assistance, and a list of all hazardous waste disposal facilities In 18 states In the Midwest. The Kentucky Department of Natural Resources and Environmental Protection distributes a list of names and locations of all permitted landfills and sanitary landfills In the state. *Th1s list Is based on a limited sampling of state solid waste agencies. This Information Is provided In order to acquaint the user with the kind of Information sometimes available on the state level. 198 APPENDIX C INFORMATION ON WASTE DISPOSAL PRACTICES OF SELECTED INDUSTRIES 199 Table C-1. Summary of Hazardous Waste Generation and Disposal in 1980 for Selected Chemical Manufacturing and Petroleum Refining Industrial Segments by EPA Region (All quantities in thousands of wet kkg) © CD ID • • E C 1 CM 3 •— M- ON © c *4- ON — •— o CM o *4- O L. © +~ L_ ** © | — CO Cl © © L. 4- O © E © 4- L. © CL ID o m vO r- r- .— ON r- — M- © • • E U 1 CM *— ON in CM — r- — TD © — 3 CD *4- CM in C TD — © C s- © ON — •— O — + C (M O c — O i_ •— •» — •— O 4— c •— 4— — © © — o M- O CO CL l_ © © 6 TD © 4- o vO CM r- m VO in r- r- — CD c •—) O in in CM rn CD in in o © © c f- — co CM ON o — — — O C TD © C ON CD CD o <0 o r** co CM ID — © * u vO — — -O O c O CD © cr < CL LU O — CMOtncOM-M-O^- ^ n in ki — Tf m id ^ 00 ON © vs. ■O CO o c — • © (N ON — M- — M-CMOK^OCs| — v cm in r- — s ID O o •— © 4 - 4 - 4 - © • — ID -C ID © 4 - 1 c c c ' 4 - 3 3 CL >* ' 4 — ID o .. CM ID 00 — CM © O L- © © 4 - __ oo CO 4 - O m o g 1 - — c c 3 3 c c c c c 3 3 3 3 3 CO CM — — CO CD CD KN K'l 00 CO m m “ - > > CO in CO CM o l_ 4- (D 3 E © 41 O cu 1 t © ON ON ON o — o m co © vO TD •— 4- CO in m — co m — vO o CO C O vO — o rn O • CD © h- CM 00 in ID TD O 3 CL ID C ID © C •— < o © ID © cn ~o 3 C © E 4- © © L_ L. a) +- © * © 4 — ID (0 * ID C © c © > o (D (D C ID © l_ o c © -C Q. ID U c © CD l_ o ID 3 o © c © © o (D 201 ^Sixty-five separate waste streams included in this estimate. c Estimate includes waste streams K048, K049, K050, K05I, as well as nine other streams consisting of spent feedstocks mi seel laneous sludges, and tank bottoms. ^Estimate includes three waste streams; acid sludges, caustic sludges, and spent clay. e Range of this estimate is^25$. Table C-2. Hazardous Waste Constituents - Petroleum Rerefining (SIC 2992) • C r—1 CNJ • CO r^i 00 CO rH • rH JO r-H CNJ to OO Cl. CO CO 00 (Ti LD CNJ 00 3 00 CTO • • C-J • • • CO r-H • L- to • • o to O • • • •r— o o • rH to X3 • U) 4-> >0 0O 00 *3' • CNJ C L O • • • CD “O o o • r-H 3 —' to ■M •r- c 4-» • CL) to oo GO to CO 3 C r-H 03 • • • • 4-> o CO to CO •r— o • CO r-H • to 4—* L- to ro C CD • o >0 u to oo • CNJ cn c • • • CD 2E CNJ o • CO 4-» to 03 lO JD o Q o 2 8 to r*— 8 o to 8 o CD -,— •t •* 0> L. o CO to CNJ rH CNJ Nl 03 zc “O o o • • 8 •f— v£> l£> o •» • • •» < r-H r-H r-H • • r-H to CD cn ■O 3 r — to CD L- § CD -C 4-» 4-» o CD to 4-» > 03 X5 *3 try 3 3 *“• r— O u to • r* to 4-» 4-> i — "O to c try •r— 3 CD <-> 03 CL O < <_> U0 h- *3 XT CL l/> 5 to T3 C 3 O CL § u 8L tO V- O o. to 3 OJ o u * a m 3 CT o CL * X £ & -J 8 8 VD IT» 8 8 in in 8 8 —« CD ^ «/l D to • >% ■h 3 ^ O T3 _ fe " >> O 8 8 8 8 n ^ ^ • • • • S in O ^-i cm r^- ft *-» s m m o» O U* i/» •*- -*-* u XJ i/> O) 3 Jd u «J < <_> o 5- u c 0) CL m QJ in U- *— 3 -O •O 4-» lj m u •*- — 9 *-» S S' 40 f- u x a m m T5 40 0» -O 4 -» 40 re <4 •“ o CD O' i_ 8 Z c * > L. 3 o go 203 Table C-4. Hazardous Waste Constituents - Petroleum Refining Waste types and hazardous constituents Waste types Constituents Leaded gasoline sludge Cooling tower sludge Crude tank bottoms Dissolved air flotation (DAF) float Exchanger bundle cleaning sludge Slop oil emulsion solids Once-through cooling water sludge Waste bio sludge Storm water silt Spent lime from boiler feedwater treatment Kerosene filter clays Nonleaded tank bottoms API separator sludge Lube oil filter clays FCC catalyst fines Coke fines Neutralized hydrofluoric acid alkylation sludge Organic lead Heavy metals Oil and heavy Oil and heavy Oil and heavy Oil and heavy Oil and heavy Oil and heavy Oil and heavy Oil and heavy Oil and heavy Oil and heavy Oil and heavy Oil and heavy Heavy metals Heavy metals Oil and heavy apors, phenols, metals metals metals metals metals metals metals metals metals metals metals metals metals and heavy metals Source: Van Noordwyk 1980. 204 Table C-5. Disposal Practices - Petroleum Refining Industrial hazardous waste quantities by disposal method Mg/year, 1977 (wet basis) Method Onsite « Offsite Public Offsite Landf111 355,000 428,000 107,000 L agoon 284,000 • • • 289,000 Landspread Incinerate 334,000 40,000 ... j ... i 4,000 Totals 1,013,000 428,000 400,000 Total petroleum refining Mg/year, 1977 (wet basis) Industry hazardous waste: 1,840,000 Source: Van Noordwyk 1980. 205 Table C-6. Disposal Practices - Organic Chemicals (SIC 2861, 2865, 2869, except 28694) Industrial hazardous waste quantities by disposal method Mg/year, 1977 (wet basis) Method Landf 111 Incineration Controlled Uncontrolled Deep well Biological treatment/1agoon Recovery Landf arm Totals Quantities Onsite Offsite 3 483,000 113,000 2,250,000 51,000 b (699,000) . . . (1,550,000) . . . 6,540,000 . . . 565,000 . . . 267,000 . . . NA C ... -10,100,000 164,000 d Total organic chemicals Industry hazardous waste: 10,300,000 Mg/year, 1977 (wet basis) Predominantly private except for minor portions (<20%) disposed of legally. Illegally, or unknowingly In municipal landfills and/or Incinerators b Larqely controlled (>90%) due to regulations which contract Incinerator operations must satisfy to destroy a variety of wastes |;Not available d The amount given here Is believed to be low. The actual quantity disposed of offsite Is believed to be between 5 and 15 percent of the total. Source: Van Noordwyk 1980. 206 Table C-7. Hazardous Waste Treatment/Disposal Methods - Selected Organic Chemical Plants CO *4- 3 in o C c C o OO in o O CM ro «r vo in 4-> • • c « 0 - o> ao CM O 00 ro >— &) s *— io cm ««r u i ■* w 4-» t- 04 o p Q. »— ■S * in 4-> c no co <— ao CT> ro o «c O o 1— a» CO o CMinr-, O N O N CM r— in cm o C O in i. CM CT» CO lO i— <*• «=c >• UJ □ — r— fN. oo r— 10 u". vo r- 10 in m cm CM *— UD 1 in o * in c o r- 0J H- •O E 3 3*— C *— CO C O 3 C -M U 4i * no crv *— oc ou/i o < cm in ■— oocnjn z tvNfl-rocomvo • A a «> r a « O S ON (\l V i— M cn CO UD CO C\J r- •- CM o o o o ID VO in in cm in E m r— at CO < 4 - m t- A—% 4 -> O 3 4 -* m ro oo m in in *— id CM O O O in • • • ■ • 9 • # ■ • ►— l- TO r— CO l-N inmscMO in **■ >. _ - o E M in 3 <0 o a« = m 3 * 4 - in O 3 O m l_ 0 J ? 04 E O in oo *— NOMr-r- cr> cn. JO CO 4 -* CD in in ro CM *— r— CM E ni in C. 3 lO fO 4-4 z: a: 3 in «r r^. c o o CT 1 cO _ 1 •M i — C C ca O 04 in O ■zs CL TD O cO in ai a> a; ■r— in X3 r— •c“J W- O in c 0) r— C 4— c 04 o r— O »— i o "3 o • 1 — r-— l_ r— •l — U1 r* C O 4-4 o 4-» *— CO 4-> CO i- r— cO t- C r— O >> £ r— CO W- o D. J- 4-> o 04 •*- t- £ t- f— l_ w 4 J +-> •r— 04 C o 3 C74 04 co o •r— 04 c C >4- C o c O > >4- 4-C <4- C aj o OJ -o *T~ c_> ZD Q-<— o -o U T4 *r- • 1 — 4-» C u 04 O O C b~ 207 ** NA indicates Not Available Table C-8. Hazardous Waste Treatment/Disposal Methods at Selected Organic Chemical Plant Sites 3 Individual Hazardous Waste Stream Liquid tars, still bottoms and process residues Liquid tars and oils (still bottoms) Liquid tars (still bottoms) Waste water, condensate Liquid tars Liquid tars and oils Liquid, tars and oils Liquid, tars and oils Liquid, oils (distillation residue) Semi-solid phenolic wastes Solid, spent activated carbon Liquid process wastes (phenols, alcohols, etc.) Liquid, dispersed In water organicsl with metal catalyst 3 Liquid, mixed process waste slurry in water Liquid tars, reactor byproduct Liquid tars, byproduct Liquid organic wastes Solid organic wastes and trash Fluid residues Fluid residues, miscellaneous Sludge, filter residues Solid reactor residues Disposal Process Actual Quantity metric tons/yr Incineration, uncon¬ trolled, energy recovery 17,800 Landfi11 300 Incineration, controlled 300 Incineration, controlled 7,600 Landfill 50 Landfill 140 Landfill 90 Landfill 50 Landfill 50 Landfill, drummed 70 Recovery Not Available Incineration, controlled 1,600 Incinerator controlled^ Landfill, drummed | 21,000 Deep wel1 254,000 4 Incinerator, uncontrolled 1,800 Incinerator, uncontrolled 500 Contractor landfill 200 Contractor landfill 200 Incineration, uncontrolled. 14,100 energy recovery 1,600 Landfi11 360 Landfill 160 208 Table C-8. (Continued) Individual Hazardous Waste Stream Solid residual pitch Solid, spent metal oxide catalyst Fluid, reactor residue j Fluid, reactor recycle > Fluid, still heads ' Solid, spent metal catalyst Liquid (thick), reactor residue Semi-solid residue Liquid, wash water waste Liquid, activated sludge from wash water waste Liquid, activated sludge, tar Liquid, activated sludge Solids, filter residues Liquid reaction waste Liquid purification waste Liquid activated sludge from water-phase wastes Liquid still bottoms Liquid still bottoms Liquid, contaminated steam condensate Liquid, contaminated wash water Liquid, activated sludge from aqueous chloroaromatic wastes Liquid, activated sludge from aqueous chloroaromatic wastes Actual Quantity, Disposal Process metric tons/yr Landfill 830 Recovery and byproduct sales 60 Incineration, 170 uncontrolled, 60 energy recovery 130 Recovery and recycle 14 Incineration, uncontrolled. 680 energy recovery Landfill 16 Activated sludge and lagoon^ 1,000 Incineration, control led 90 Incinerator, controlled 4 Incineration, controlled 36 Incineration, controlled 70 Deep well injection 22,700 Deep well injection 11 Incineration, controlled 5 Incineration, controlled 800 Incineration, controlled 800 Deep well injection 90 ' Deep well Injection 30 Incineration, controlled 20 Incineration, controlled 80 209 Table C-8. (Continued) Actual Quantity, Individual Hazardous Waste Stream Disposal Process metric tons/yr Liquid still heavy ends Incineration, control led 500 Liquid, phenolic contaminated wash water Activated sludge and lagoon 90 Liquid, activated sludge from wash water waste Incineration, control led 3 Liquid still bottoms Incineration, control led 70 Liquid, reprocessing tars Incineration, control led 200 Liquid, neutralization products Deep well Injection 6,000 Liquid, scrubber waste Incineration, controlled (salt ash to industrial outfal1) 400 Semi-solid, filter cake Landfi11 280 Liquid, still bottoms Incineration, controlled (salt ash to industrial outfall) 1,100 Liquid, wash water Activated sludge and lagoon 600 Liquid, activated sludge from wash water waste Incineration, control 1ed 100 Liquid, contaminated condensate Activated sludge and lagoon 20 Liquid, activated sludge from contaminated condensate Incineration, controlled 4 Semi-solid, filter cake Landfi11 500 Liquid, wash-down wastes Activated sludge and lagoon 100 Liquid, activated sludge from wash-down wastes Incineration, control 1ed 20 Solid, spent ion exchange resin Landfi11 1 Solid, spent charcoal Thermal regeneration (recovery) 50 Solid, wastes/residues Incineration, uncontrol 1ed Hot Avallabl 210 Table C-8. (Continued) Actual Quantity, Individual Hazardous Waste Stream Disposal Process metric tons/yr Liquid, activated sludge from wastewater Evaporation (spread on farm land) Not Available Liquid, neutralized A1 salt solution Contractor deep well, landfill and incineration Not Available Liquid wastes, toxic Contractor disposal Not Available Liquid, oil sludge from waste water Contractor disposal Hot Available Solid, catalyst residue, N1 compounds Recovery (N1 - 100%) 3 Solid, catalyst residue, Cr compounds Recovery (Cr - 100%) <1 Solid, catalyst residue, SIC compounds Recovery 30 Liquid, distillation residue Incineration, uncontrol led energy recovery 2,700 Solid, catalyst residue, N1 compounds Recovery (N1 - 100%) 3 Solid, catalyst residue, Cr compounds Recovery (Cr - 100%) <1 Solid, catalyst residue, SIC compounds Recovery 20 Fluid, aromatic residues Incineration, uncontrolled jenergy recovery 260 Solid, spent catalyst, Sb salt Landfill (encapsulated) 20 Solid, spent catalyst, Cu and oxides Recovery (Cu — 100%) 3 Solid, spent catalyst (mol-sleve) Landfl11 5 Liquid, viscous Incineration, uncontrolled energy recovery 8,200 Solid, spent catalyst, N1 compounds Recovery (N1 - 100%) 20 i Solid, spent catalyst, Cr compounds Recovery (Cr - 100%) <1 211 Table C-8. (Continued) Actual quantity, Individual Hazardous Waste Stream Disposal Process metric tons/yr So 1 id, spent catalyst, SIC compounds Solid, spent catalyst, Co compounds Solid, waste Na metal Fluid, organic residue Fluid, organic cyclic gums Liquid, dryer waste, Ca salts Liquid, dryer waste, Ca salts Liquid, activated sludge Solid, filter wastes Liquid, vent scrubber wastes Liquid, tar dump Liquid, organlcs/acid Liquid, residues Semi-solid, chlorinated hydrocarbon heavies Semi-solid, lead compound sludge Fluid, reactor byproduct Solid, copper compound residues Solid, Cr compound residues Recovery 20 Incineration, uncontrolled, energy recovery 3 Landfi11 1 Incineration, uncontrolled energy recovery ( 300 ( 9,000 Deep wel1 Injection 14 Deep wel1 Injection 5 Incineration, controlled 230 Incinerator^ 4 Activated sludge and lagoon 7 6,500 Activated sludge and lagoon 7 45 Activated sludge and lagoon 7 2,300 Activated sludge and lagoon 7 90 Deep well injection 13,600 Recovery furnace 9,100 Incineration, control led, energy recovery 1,600 Recovery 3 Recovery 1 212 Table C-8. (Continued) o Composite Hazardous Waste Streams Disposal Process Actual Quantity metric tons/yr 4 Liquid hazardous waste streams Recovery 2,350 5 Liquid hazardous waste streams Incineration, controlled 3,860 10 Liquid hazardous waste streams Incineration, uncontrolled 10,000 14 Liquid hazardous waste streams Landfill 1,100 1 2 3 4 5 6 7 8 9 23 Solid hazardous waste streams Landfill 5.800 9 4 Liquid or solid hazardous waste streams Lagooned Not Available 5 Liquid or solid hazardous waste streams Contractor Incineration 2,100 5 Liquid or solid hazardous Contractor landfill 4,700 waste streams 1. 90% organics. 2. Metal recovered from incinerator ash. 3. About 0.5% organics in water. 4. Highly dangerous compound - 700 metric tons/year. Moderately dangerous compound - 600 metric tons/year. 5. Salts to outfall. 6. Soluble salts to industrial outfall, silicates to landfill. 7. Salts to industrial outfall. 8. Data composited to protect proprietary information. 9. Includes 800 metric tons stored hazardous wastes. a This table provides the reader with general information on common disposal methods for various types of wastes, based on a survey of organic chemical plants. Source: TRW 1975. 213 APPENDIX D INFORMATION IN SUPPORT OF STAGE III 215 Exhibit D-l. The Hazardous Waste Data Management System (HWDMS) The Hazardous Waste Data Management System (HWDMS) maintained by the EPA State Programs and Resource Recovery Division of the EPA Office of Solid Waste (OSW) provides a computerized means of tracking permit applications for the treatment/storage/dlsposal (TSD) of hazardous waste. The system can be accessed by SIC code to obtain the names and locations of all facilities within an Industry group that have applied for permission to treat, store, or dispose of any hazardous wastes. A complete printout of permit application data Is available at the EPA Office of Solid Waste, arranged by zip code. This must be consulted manually. For each location, the printout provides the type of hazardous waste facility (l.e., landfill, Incinerator, etc.) and Its proposed capacity. See Table D-4 In Appendix D for a list of the TSD process codes and capacity units In the data base. The system can also Identify waste stream types and volumes handled by each on-site disposal practice, but these data are considered unreliable by OSW staff and thus are useless at the present time. Both on- and off-site facilities are listed and In the near future, HWDMS will Incorporate a "tag" that distinguishes between on- and off-site facilities. A recent summary compilation of hazardous waste sites Included In the HWDMS data base Is provided as Table D-7 In Appendix D. The HWDMS Is most useful In Stages III and IV. For Stage III, It can determine what kind on on-site facilities are available In the geographic area of Interest In order to confirm or correct data obtained from other sources. This can be accomplished by requesting a printout of the names and locations of all hazardous waste TSD facilities In the study area. More detailed Information on these facilities can then be obtained by examining the printout of permit application data (by EPA Region) available at OSW. For Stage IV, the system will supply actual locations; commercial (off-site) waste handlers may be located by using the commercial "tag"; It Is not known at this time whether these facilities can be extracted using the waste disposal SIC code (4953). Plants lacking on-site facilities may be assumed to dispose of hazardous waste at the nearest off-site facility possessing the requisite treatment type In the absence of better Information. V Note the following caveats: • The EPA staff has not had the time to verify the application data before entering It In the HWDMS. SIC codes and TSD Information may not accurately reflect the actual plans of the facility. As EPA reviews applications, however, appropriate corrections will be made In the applications and the data base. 217 • Because the application Information Is submitted In advance of operations, the proposed facilities and types of wastes treated may not be representative of the current conditions. For example, a proposed Incinerator may not be built, and the list of wastes handled Includes all wastes that might be treated. • Many unnecessary and misleading entries are Included In the data base. For example, gas station owners In some areas thought that they had to apply for a TSD permit, and many corporate headquarters mistakenly applied for a TSD permit, even though no hazardous waste Is handled on-site. Therefore, any retrieval should be examined carefully and discussed with OSW Staff. 218 Table D-l. POTWs: Treatment Populations - Present and Projected, Resident and Nonresident (in Thousands) 3 *0 CD > u Q) O to 00 •- c di cj u Q) Cl. U O CO CD 0) -»-> 01 £ o CO CD CD C *> T? CD U 10 a> <3- r- u-> CO O in C\J iX P— CD r-. ^ CO UD "3 in vD * 3 * CO •— o — inioooocoo 1 O CO 00 CO O CO o 0—0 CO m cd co o cnj in R ~ O iO r-~ p- cnj in in — in — o CNJ CO CO o o — in in in o co — ^ o — *r CO CNJ P- CNJ CNJ CO in — co cnj < 5 * n a» o 10 co cnj m cnj m p-> r** co in — a* ao — — CNJ r- CNJ CNJ * 3 - — O v£> 00 — p- 3 CO O 3 - in CO CD R 8 £ CNJ CNI ci co in CNJ vO r-» CNJ O — in CNI O ^ 3 * — — CO +J CD CO CO in CO CNJ m 0 0 CO CD in 0 CO CNJ CNJ CD CO 0 00 CNJ r» O co co m CO CNJ r- O p— ^ CO c 1 4 -> U c 0 z 0 0 CNJ 0 0 CO CD CO 5 co CD — CO ^ 3 - CNJ — <£> lO 00 CNJ m CNJ CNJ — 00 CO — D in § cR CM CNJ § O CNJ CM O 00 in CNI m m ,885 463 CD CNJ r— p- r-> . r— CO 0 m 00 in 480 § CD in p- ** in CD 5 CNJ CO 482 P““ in co 605 362 O in r- co 0 P- in CNJ »— r- CD CNJ ^ 3 * CO CD CO CNJ *— r- CNJ CNJ CO X> CNJ r— CO #— m r- CNJ D CD s 0 O in CNJ in CNJ in 0 CO m m 0 0 co CD p^ in r- m. m. * m. * CO CNJ CNJ CNJ CNJ CO CO m in CNJ CNI co < 3 * • 3 * n CD ^3 CNI r— r-» r— CD CNJ — — 5 to CD r— S- 8 4-> >r > . r— 03 n CD CL x: >> O • r— u 03 to 03 O. to CD O l/> c 8 • r* CD 14 - to >> C "O n c 4-» • r— • r* 03 Q to •r* rg 03 03 l_ -*-> i- O 03 03 • 1 — 03 03 c x: 03 0 10 03 J* t- X l- P 03 C l/> 0 03 u 03 T3 O c to CJ 03 u CD to to n C to 03 o3 - -L-> £k l/> ISI 03 • r- O c 03 4-» L- t- 03 J= .r- 03 to -t-> »r* c to x: C to to 03 03 0 5 03 • r- r— c r— to O 9 ^ 03 T3 5 c C n • r— L. to u c to to C -Q > 3 2 5 4-» r— r— i- U (3 8 0 8 . r- CU 03 ■O c 0 03 CD O 03 03 03 • r* . r— . *— £ CD CD CD CD CD CD 00 < < < < 0 Q Ll. C3 X »—1 ►—1 HH »—1 _j X z: X X z : z: z: Z Z z Z z Z 219 -o Q) > L. dJ O in 00 .— c 01 u J- r— CO r- CO U1 (T> CNJ lDlOCO O O CO CNJ CO CO M O CO O -g , vDr^r^i/)r^vD^TUD^'OOCO , 3 , ^vD^rr*-p^ ^ if) C\1 o 00 O) O' c — CD U-O o • L- (/I 0) -*-> cr So 00 ro o o ro cnj o — ro lO OsJ 00 lO »X> vO COCO — — OOOOOO ro — cnj rsj 00 O' s£> in ro 00 00 O' $ $ r- ro in ^ O' o ro ro lo o uo ro * 3 * o r- i£> lD cnj ro co cnj o co co cnj ro co uo ro co — •— *— lo o co ^ in o 00 O' CNI 00 o* 00 CNJ CT> CO — r- CNJ *r »x> O ro o o o ro ro r- lo ro uo *— ro cnj j) in in o — oo — cnj i^roa^rofroco^in^r- cnj CO K3* CNI *— ^ 1^- U0 " “ - ---- — cnj^t*— O'-CNjcoror-^rro r- CNJ lO UO CNJ uo CO CNJ *— oo — ro cnj o r—■ © CNJ ro r— lO uo vO o CO CO O' *3 r- a> uo CNJ cr> 00 00 o CNI r-» 450 31 114 r- 00 — — LO¬ CO — 96 *3“ CNJ 00 UO O CNJ CNJ CNJ co uo co CO ro CNJ CNI rO r^3 in c C rT3 Q u *o . r— fQ ■o • r- rO L. c r— 4-> C •— 4-> C rQ in o dJ no oo o o c *T3 o O c •— oo r0 o H- r— _1 L. rT3 r— l_ -* d> o o> c C • r— in < rtf rT3 ffl > in 03 rO O rT3 l_ IP > c ro oc: FH ►— O O F HH O O m -*-> •*— •— in o> ro • r> (- o o c >» in c c c > c c CJ u o H— c >— dJ .c JZ -C o in jC J= • r- -F> o c 4-> c rfl jC E C7> jC +-> u E l_ E • o> • o O .C -* i_ CD J= o o a> o; 4-> QJ •»- 5 4 . r— F D • D no • p- • OO z z o o O Q_ a: oo oo i— ►— 10 > > 3 C3 z a. Q- z> 3 220 CD 03 +-> O c 8 U. I o n 03 c 03 ■o 03 CD 03 “O “O A - E • r - c “5 03 4-> > 03 • r— 03 o 4-> 03 o > CD CD -4-* C 03 03 U CD o 03 3 4-> l_ CL 03 u CD U X3 *D CD h- 03 Q. >> 03 C 4-» C- r— 3 >> 03 03 CD 03 03 CD 03 CD -*-> A cz JC 0) C CD •*— -*-> -4-> •»- -*-> 4-> U < U C > U 3 T3 O 0) 4- CD o CD o cu r E O 03 CD • r— • f— A «4-> -4-> CJ 5 03 V4- E CD 3 03 -*-> 03 o> i- o •r- 03 03 t- Ql r— c c — U 03 4-> o o O CD ■»-> Ql -*-> < 03 • r- CJ 03 CD O Q. 4-> UJ -4-> 03 CD CD Z LU CD 03 CD U C 03 OO 4-> r— 4- 03 0J *r- U ID C 3 O Z > *D O 03 Q. C CD •«- 03 4- ■o =3 03 CD 03 -*-> CD O • r— Cl 03 CJ C C CD 03 >> "O 03 3 CD 03 03 C_ -O 03 U O > 03 C- 4-> 3 JC CJ T- 03 CO "O CD CD 03 !o >> 4-> 03 -r- C 03 (J 03 u CD •> 4-» r- O L- 03 -*-> 03 03 03 O -r- 03 01 s. r— CJ L UJ J L. Q 03 u 03 -*-> 03 O >> 03 rt 4-> fl) Ql CD »— jC C -C o O 03 3 5 03 4-» 03 4-> P Q. o 4-> Q >> C O CD C 03 • (J «*-> 03 Ql 4-> • f“ c CD CD • r— c •f— • 03 4-> S- 4- *— 4- Q3 03 T3 >> 03 O -r~ O JZ T3 03 T3 4-» r— *C3 4-> CJ 4-> •r- -O 03 • r- C 03 -*-> 03 03 CD 3 4-> u 03 03 I* c 4- 03 4- CD r- c o CD 4-> E 03 03 c CD -*-> CD c CD 4-> c r— . r— 03 3 03 s 03 u +j 0) 3 03 l- 03 E 3 03 03 CJ CD t- +-> Ql • ^3 CL • r- 3 O 03 L. 03 s. “O > CD U C 03 CD 03 03 •r“ O 03 l r l- 03 JZ U 03 J Q) J >> 03 03 U 4-> -C 03 CD c u 03 O 4-> -C 03 >> m jt3 CD c O) 4-> S- 03 r- E 03 03 c 4- 4-> x: •r— CD • r— o >> -4-> 03 03 QJ 1- c > 03 03 L. cn c 03 u CD U 03 A CD U 03 CJ *— .c 3 I Q CD O "O CD -O 03 CD CD C 03 O 03 L. 03 CD CJ • r* > U CD CD C -C CD c T3 C 03 03 CD S- 03 CD CJ • r— > L- CJ CD CD c o CD c S r- CD CD -M l_ C CD 0) -*-> T3 3 03 c 4-> -4-> - C 03 03 -*-> • r* 03 03 o 03 4- 03 S- CJ 03 CD r— 4-> 03 z 03 4-> O C- • r- 22 S- 03 03 -*-> -4-> 03 c >> 03 E 3— CD “O 4-> 03 u c “O o -Q CJ • r— -C 03 CD 03 03 4- 03 3 CL 4-> CD 4-» -*-> U O c r— 3 CD 03 CD C 03 03 03 4-> m u C -4-> 03 . r— c 03 jC C r— P c *o o 03 > • r— U 4-> 03 OJ 03 L • r— 03 4-> < . r— -*-> CJ > 03 CD 4-» CD UJ 03 “O r— »r* 4_> 03 CL N 03 CO U 03 4-> 03 > 03 CD A r— O 03 TJ o 3 L. 03 03 03 3 CO 03 Ql 3 c O' 03 U CJ 5- U 03 Cl -C i— 03 CD 4-> • r* 03 c U O 03 U CD 4- O 03 -C C •*- T3 CD 03 CD -+-> .r- O CJ CD CD 03 -C • r- CD 3 4-> 03 03 03 4-» c 03 4-> O CD Q. Ql CD 3 -*-> r— • r— (. 03 A c r— CD •*—* C 03 03 U CD • P“ 03 o 03 CD o ■*-> T3 03 > -C CD > • 03 4- O 03 CD C 4-> 03 03 u C 4-> 03 N T3 C 03 C T3 o 03 • “D • r- T3 3 O CJ) a> •f* 03 f— CD 03 00 L. 03 o r— ID E CD r— -4-> 3 C > CD 0 +> CO CJ i_ >> 03 (. 03 CL O U p CD CD c 03 03 03 L. < o i — O • r— 03 p • p- r— • r* Q_ 03 4- 3 Ql 4-» bO < 5 r— 4-> u 4-» Cl 03 Q. CD 03 03 O C O 4-> CJ 4-» LU CD U • L. CZ CD o Ql c O c uo •— 03 1— 03 >> CD CD 03 CD 03 Z> C O •- TD 03 • C 5 > O c 03 CD 03 03 < .. 03 > s o o 03 • r- r— CD C “O 03 *— Q_ UJ 03 r— < CD -C -*-> 03 03 03 O • r— U •p- 00 CJ -Q 03 UJ U CD u -4-> -f-> 4- CD c E 03 U 03 A 00 03 3 03 03 O 03 C 03 O A >> 3 ►— \— Q- 03 5 U CJ 01 z CD »— o 03 A O T3 03 4- 40 221 Table D-2. POTWs: Average Domestic Flows by State - Present, Projected, and Percent Change (Thousands of Cubic Meters per Day) 3 U c CT ■S c » 5 m o o O' r-» ^ iO o o CSJ r— m CSJ m O' in o *3* iO co co m m CO CSJ CSJ CT' m r-* co r». co in O' in CSJ os CO in r— CO O' in OJ CO CSJ m in in ^r C\J O' 00 CQ r— CSJ CSJ in Os in in r^- r— in CO in in r-» r- Os CO in in m in p— in r- CO m p— in in o O' in <0 r— CO O “ cm o m O' m f— O' in co p-~ p-» 3 uo uo o f—• CM O' CO co O' in O CO s r— O O' o CSJ s CSJ 00 m CSJ r— uo p-* o CO 00 in O' m in CM ^r o O' o o O' 00 m CM p-> m uo r-> CD CM o O' CO p—. 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U3 uo in o fl) rQ 07 u u QJ o o L. > 3 < C3 z O- CL > 223 U.S. TOTALS 97,117 80,679 479 130,260 109,981 654 u *o 05 5 • r* 05 4-> • CJ X) *D c • CD c LL. •i- D CD 05 CD CD 2 OJ o 4-> u -X • r— l o oo U • — CD CD 05 r— -*-> • 2 c Q a c 3 •*-> u- r— 05 c P • r” C 05 CZ r— r“ CD Q O L 3, -r- 05 • r- *0 oo 4-> O O oo 05 \ ft CD E 8 c If 4-> 05 •*- -*-> C CD O CD 05 3 O E U C +-> 05 • r ~ l_ u_ 05 Q c 2 4-» *o 4-> 4-> 05 X E 05 05 05 c c 05 T r- U C 05 05 oo t_ >> U- Q. r— 4-> • r— *o 00 •r- 05 4-> 5- 05 •— C4- 05 r— O 05 4-> • r* -s CD U -*-> 00 4-> CD co c CD c*- 05 CL 05 CD 05 05 05 05 C U .Q •— 4-> 05 € •f" oo c *o *o 05 JC X> O c < 05 U -*-> 05 05 *0 c 05 CD CL > 05 C C J -*-> LU • r* CD 00 L •*“ 05 O *o r— c c/o 05 •r- ro 4-> c*. c 05 05 3 (J -C J 0) • u- 05 r — 05 4-> 05 -D CL C U c 05 u 4-> U C o 2 00 .r- • r— c < CD u > U 8 s »— ID <4- C r- -O c CD “D ° § * >> U 4-> 4-> <4_ O •r- 4-> t 8 ^ 05 *— ro 15 ^4- 3 S’ O *r- 4-» CD 2 O ^ c >> C 03 (D CD •— L >> L Q. 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V4- > >> t Q. 4-> 2 CD >> CD > o rg 05 E f— W- f— CD < T5 O CD 05 “D O <4- oo CJ 5- • 05 05 U L •r- C CX) O 05 •r- Ql r— 05 U L 05 L. 05 CD 1 4-> 05 r— L 4—> 05 4-> 4-> ■O O 3 CD D -Q 15 • CL U 2 CD c c 4-> 05 O E O E 15 O c D -♦-> CL • u r- CO O CO 00 4-> *D • r— O Q CD CD < • r— L CD 1- CD u C U- L O >) 05 V*- 05 L *4- r— 05 g • r— 4-» u. n u V4- 05 > O • 4-> E 3 u c o O 05 4-> ■O c g O 3 4—> •r* Q) 4-> *o o T ■+-> 2 CD • r— E X5 CJ CL 4-> E • 05 CO T5 oo e E 05 CD 4—> 05 C\J +-> c E C • r— 05 U CD <4- U di 05 15 ci 05 *— 15 O ,r ” 05 05 Q. U •r- C o X F 05 *o CD 05 o L C -C Ql E 05 -D •— 05 n L L -r- L <4- O 5- O r— 15 "O CD Q 4-» r— 05 -*-> L • f - Oft u CL U 15 T? 00 03 4-> o TD 4-> LU r—- C 05 05 CD 4—> 3 5 CD +•> 05 0j • O 05 C <4- CJ 05 CJ -C C o 05 O 3 p ° CL L • r - O c CD L 4-> • r* 4-> — 05 CD CD < a_ 05 CJ L. 15 o oo 224 Table D-3. State Solid Waste Agencies U.S. Environmental Protection Agency Office of Solid Waste Alabama Alfred S. Chipley, Director Division of Solid Waste and Vector Control Department of Public Health State Office Building Montgomery, Alabama 36104 FTS 8-534-7700 OFF (205) 832-6728 Alaska Richard Stokes Solid Waste Program Department of Environmental Conservation Pouch 0 Juneau, Alaska 99811 Seattle FTS Operator 399-0150 OFF (907) 465-2635 American Samoa Randy Morris, General Manager Water, Sewer and Solid Waste Division Department of Public Works Pago Pago, American Samoa 96799 Overseas Operator (Comm. Call) Arizona John H7 Beck, Chief Bureau of Sanitation Department of Health Services 411 North 24th Street Phoenix, Arizona 85008 FTS 8-765-1160 OFF (602) 255-1160 Arkansas Doice Hughes, Acting Chief Solid Waste Control Division Department of Pollution Control and Ecology P. 0. Box 9583 8001 National Drive Little Rock, Arkansas 72219 FTS Operator 740-5011 OFF (501) 561-7444 California Jerry Prod, Chairman State Solid Waste Management Board P. O. Box 1743 1020 9th Street Sacramento, California 95808 FTS 8-552-3330 OFF (916) 322-3330 Dr. Harvey Collins, Chief Hazardous Material Management Section Department of Health Services 714 P Street Sacramento, California 95814 FTS 8-552-2337 OFF (916) 322-2337 Connecticut Charles Kurker, Director Solid Waste Management Programs Department of Environmental Protectioi 122 Washington Street Hartford, Connecticut 06106 FTS 8-641-3672 OFF (203) 549-6390 Russell I.. Brenneman, President Connecticut Resource Recovery Authority Suite 1305 60 Washington Street Hartford, Connecticut 06115 OFF (203) 549-6390 Colorado Orvilie~F. Stoddard Department of Health 4210 East Eleventh Street Denver, Colorado 80220 FTS Operator 327-0111 OFF (303) 320-8333 225 Table D-3. (Continued) Delaware T. Lee Go, Chief Solid Waste Section Department of National Resources and Environmental Control Edward Tatnall Building Dover, Delaware 19901 FTS Operator 487-6011 OFF (302) 678-4781 District of Columbia Malcolm Hope - Department of Environmental Services 415 12th Street, N. W. Washington, D. C. 20Q04 FTS 8-727-5701 OFF (202) 727-5701 Florida Ralph Baker, Acting Environmental Administrator Solid Waste Management Program Department of Environmental Regulation Twin Towers Office Building 2600 Blair Stone Road Tallahassee, Florida 32301 FTS 8-946-2011 OFF (904) 488-0300 Georgia Moses N. McCall, III, Chief Land Protection Branch Environmental Protection Division Department of Natural Resources Room 822 270 Washington Street, S.W. Atlanta, Georgia 30334 OFF (404) 656-2833 Guam Dr. O. V. Natarajan, Admin. EPA, Government of Guam P. 0. Box 2999 Agana, Guam 96910 Overseas Operator (Commercial Call) 646-8863 Hawaii Ralph Yukumoto Environmental Health Division Department of Health P. O. Box 3378 Honolulu, Hawaii 96801 Calif. FTS Operator 556-0220 OFF (808) 548-6410 Idaho Jerome Jankowski, Acting Chief Solid Waste Management Section Department of Health and Welfare Statehouse Boise, Idaho 83720 FTS 8-554-2287 OFF (208) 384-2287 Il linois John S. More, Manager Division of Land and Noise Pollution Control Environmental Protection Agency 2200 Churchill Drive Springfield, Illinois 62J706 FTS Operator 956-6760 OFF (217) 782-9882 Indiana David Lamm, Acting Chief Solid Waste Management Section Division of Sanitary Engineering State Board of Health 1330 West Michigan Street Indianapolis, Indiana 46206 FTS 8-336-0200 OFF (317) 633-0200 Iowa Charles C. Miller, Director Air and Land Quality Division Department of Environmental Quality Henry A. Wallace Building 900 East Grant Des Moines, Iowa 50319 FTS 8-841-8853 OFF (515) 841-8853 226 Table D-3. (Continued) Kansas Charles H. Linn, Chief Solid Waste Management Section Department of Health and Environment Topeka, Kansas 66620 FTS Operator 752-2911 OFF (913) 862-9360 Ext. 297 Kentucky Norman Schell, Director Division of Hazardous Materials and Waste Management Department for Natural Resources and Environmental Protection Capitol Plaza Tower Frankfort, Kentucky 40601 FTS 8-351-6716 OFF (502) 564-6716 Louisiana Lee Jennings, Director Office of Science, Technology and Environmental Policy P. 0. Box 44066 Baton Rouge, Louisiana 70804 FTS Operator 687-0770 OFF (504) 689-6981 G. Roy Hayes, Jr., Administrator Solid Waste & Vector Control Unit Health and Human Resources Administration P. 0. Box 60630 New Orleans, Louisiana 70160 FTS Operator 682-5137 OFF (504) 568-5137 Maine Ron Howes, Chief Division of Solid Waste Management Control Bureau of Land Quality Department of Environmental Protection State House Augusta, Maine 04333 FTS 8-868-2111 OFF (207) 289-2111 Maryland Robert Schoenhofer, Chief Planning Section Department of Natural Resources Water Resources Administration Tawes State Office Building Annapolis, Maryland 21404 FTS 8-920-3311 OFF (301) 269-3821 Massachusetts William Gaughan, Director Bureau of Solid Waste Disposal Department of Environmental Management Room 1905 Leverett Saltonstall Building 100 Cambridge Street Boston, Massachusetts 02202 OFF (617) 727-4293 Solid Waste Regulatory Anthony Cortese Division of Air and Hazardous Materials Department of Environmental Quality Engineering 600 Washington Street, Room 320 Boston, Massachusetts 02111 OFF (617) 727-2658 Hazardous Waste Regulatory Hans Bonne Industrial Waste Section Division of Water Pollution Control Department of Environmental Quality Engineering 110 Tremont Street Boston, Massachusetts 02108 OFF (617) 727-3855/6587 Michigan Mr. William G. Turney, Director Environmental Protection Bureau Department of Natural Resources Stevens T. Mason Building Box 30028 Lansing, Michigan 48909 FTS 8-253-7917 OFF (517) 373-7917 227 Table D-3. (Continued) Minnesota Louis Briemhurst , Acting Director Division of Solid Waste Pollution Control Agency 1935 West Country Road, B-2 Roseville, Minnesota 55113 FTS 8-776-7315 OFF (612) 296-7315 Mississippi Jack M. McMillan, Director Division of Solid Waste Management and Vector Control State Board of Health P. 0. Box 1700 Jackson, Mississippi 39205 FTS 8-490-4211 OFF (601) 982-6317 Missouri Robert M. Robinson, Director Solid Waste Management Program Department of Natural Resources State Office Building P. O. Box 1368 Jefferson City, Missiouri 65102 FTS Operator 276-3711 OFF (314) 751-3241 Montana Dwane L. Robertson, Chief Solid Waste Management Bureau Department of Health and Environmental Sciences 1424 9th Avenue Helena, Montana 59601 FTS 8-587-2821 OFF (406) 587-2821 Nebraska Maurice A. Bill Sheil, Chief Solid Waste Division Department of Environmental Control State House Station P. 0. Box 94877 Lincoln, Nebraska 68509 FTS 8-541-2186 OFF (402) 471-2186 Nevada H. Laver ne Rosse, Program Director Solxd Waste Management Division of Environmental Protection Department of Conservation and Natural Resources Capital Complex Capitol City, Nevada 89701 FTS Operator 470-5911 OFF (702) 885-4670 New Hampshire Thomas L. Sweeney, Chief Bureau of Solid Waste Department of Health and Welfare State Laboratory Building Hazen Drive Concord, New Hamsphire 03301 FTS 8-842-2605 OFF (603) 271-2605 New Jersey Beatrice Tylutki, Director Solid Waste Administration Division of Environmental Protection P. O. Box 1390 Trenton, New Jersey 08625 FTS 8-477-9120 OFF (609) 292-9120 New Mexico Dan Torres, Head Solid Waste Management Unit Environmental Improvement Division P. 0. Box 968 Crown Building Santa Fe, New Mexico 87503 FTS 8-476-5271 OFF (505) 827-5271 Jon Thompson, Chief Community Support Division Health and Environmental Department P. 0. Box 968 Crown Building Santa Fe, New Mexico 87503 FTS 8-476-5271 OFF (505) 827-5271 228 Table D-3. (Continued) New York Norman H. Nosenchuck, Director Division of Solid Waste Mgmt. Department of Environmental Conservation 50 Wolf Road Albany# New York 12233 FTS 8-567-6603 OFF (518) 457-6603 North Carolina Jerry Perkins# Head Solid Waste and Vector Control Department of Human Resources and Division of Health Services P. O. Box 2091 Raleigh# North Carolina 27602 FTS 8-629-2111 OFF (919) 733-2178 North Dakota Gerald Knudsen# Director Division of Waste Supply and Pollution Control Department of Health 1200 Missouri Avenue Bismarck, North Dakota 58505 FTS Operator 783-4011 OFF (701) 234-2366 Ohio Donald E. Day# Chief Office of Land Pollution Control Environmental Protection Agency P. O. 1049 Columbus, Ohio 43216 FTS 8-942-8934 OFF (614) 466-8934 Oklahoma H. A. Caves# Director Industrial and Solid Waste Division Department of Health P. 0. Box 53551 Northeast 10th & Stonewall Sts. Oklahoma City# Oklahoma 73105 OFF (405) 271-5338 Oregon Ernest A. Schmidt# Administrator Solid Waste Management Division Department of Environmental Quality 1234 S.W. Morrison Street Portland# Oregon 97205 FTS Operator 423-4111 OFF (503) 299-5913 Pennsylvania William C. Bucciarelli# Director Division of Solid Waste Management Department of Environmental Resources Fulton Building# 8th Floor P. O. Box 2063 Harrisburg# Pennsylvania 17120 FTS 8-637-7381 OFF (717) 787-7381 Puerto Rico Santos'Rohena# Associate Director Environmental Quality Board Office of the Governor Box 11488 Santurce# Puerto Rico 00910 D.C. FTS Operator 967-1221 OFF (809) 735-5140# Ext. 263/4 Lou David# Jr.# Executive Director Rhode Island Solid Waste Corporation 30 Pike Street Providence, Rhode Island 02903 OFF (401) 831-4440 South Carolina Hartsill Truesdale# Director Solid Waste Management Division Department of Health and Environmental Control J. Marion Simms Building 2600 Bull Street Columbia# South Carolina 29201 FTS 8-677-5011 OFF (803) 758-5681 Rhode Island John S. Quinn# Jr.# Chief Solid Waste Management Program Department of Environmental Management 204 Health Building Davis Street Providence# Rhode Island 02908 OFF (401) 277-2808 229 Table D-3. (Continued) South Dakota Joel Smith, Director Air Quality and Solid Waste Management Department of Environmental Protection Office Building No. 2 Pierre, South Dakota 57501 FTS Operator 783-7000 OFF (605) 224-3784 Tennessee Tom Tiesler, Director Division of Solid Waste Mgmt. Bureau of Environmental Services Department of Public Health Capitol Hill Building Nashville, Tennessee 37219 FTS 8-853-3424 OFF (615) 741-3424 Texas Jack C. Carmichael, Director Solid Waste Division Department of Health 1100 West 49th Street Austin, Texas 78756 FTS 8-734-7271 OFF (512) 458-7271 Jay Snow Solid Waste Branch Department of Water Resources 1700 North Congress P. O. Box 13246 Austin, Texas 78711 FTS 8-734-5011 OFF (512) 475-6625 Trust Territories Nachsa Siren, Chief Environmental Health Division Department of Health Office of the High Commissioner Trust Territory of the Pacific Islands Saipan, Trust Territories 96950 Overseas Operator (Comm. Call) Manuel A. Sablan, Director Office of Planning and Budget Affairs Commonwealth of No. Marinas Islands Office of the Governor Saipan, Trust Territories 96950 Overseas Operator (Commercial Call) Vermont Richard A. Valentinetti, Chief Air and Solid Waste Programs Agency of Environmental Conservation State Office Building Montpelier, Vermont 05602 FTS 8-832-3395 OFF (802) 828-3395 Virgin Islands Sammy E. Harthman, Jr. Project Coordinator Solid Waste Planning Office Department of Public Works Government of the Virgin Islands Charlotte Amalie St. Thomas, Virgin Islands 00801 OFF (809) 774-7880 Virginia William F. Gilley, Director Bureau of Solid and Hazardous Waste Management Department of Health 109 Governor Street Richmond, Virginia 23219 FTS 8-936-5271 OFF (804) 786-5271 Utah Dale Parker, Chief General Sanitation Section State Division of Health 44 Medical Drive Salt Lake City, Utah 94113 FTS Operator 588-5500 OFF (801) 533-5145 230 Table D-3. (Continued) Washington Duane Wegner, Director Land Disposal Division Department of Ecology Olympia, Washington 98504 FTS 8-434-6883 OFF (206) 753-6883 West Virginia Dale Parsons, Director Disposal Planning Department of Health 1800 Washington Street, E Charleston, West Virginia 25305 FTS 8-885-2987 OFF (304) 348-2987 Wisconsin Robert M. Krill, Director Bureau of Solid Waste Management Department of Natural Resources Box 7921 Madison, Wisconsin 53707 FTS Operator 8-366-3538 OFF (608) 266-2621 Wyoming Cnarles Porter Solid Waste Program Supervisor Department of Environmental Quality State Office Building, West Cheyenne, Wyoming 82002 FTS 8-832-9752 OFF (307) 328-9752 231 Table D-4. Hazardous Waste Treatment, Storage, and Disposal Process Codes Used in HWDMS Process Process Code Appropriate units of measure for process design capacity Storage: Container (barrel, drum, etc.) SOI Gallons or liters Tank S02 Gallons or liters Waste file S03 Cubic yards or cubic meters Surface impoundment S04 Gallons or liters Disposal: Injection well D79 Gallons or liters Landfi11 D80 Acre-feet (the volume that Land application D81 would cover one acre to a depth of one foot) or hectare-meter Acres or hectares Ocean disposal D82 Gallons per day or liters per Surface impoundment D83 day Gallons or liters Treatment: Tank T01 Gallons per day or liters per Surface impoundment T02 day Gallons per day or liters per Incinerator T03 day Tons per hour or metric tons Other (Use for physical, chemical, T04 per hour; gallons per hour or 1iters per hour Gallons per day or liters per thermal or biological treatment day processes not occurring in tanks, surface impoundments or incinerators.] 1 232 Table D-4. (continued) Unit of measure Unit of measure code Gallons G Liters L Cubic yards Y Cubic meters C Gallons per day U Liters per day V Tons per hour D Metric tons per hour W Gallons per hour E Liters per hour H Acre-feet A Hectare-meter F Acres B Hectares Q Source: EPA Form 3510-3. 233 Table D-5. Information on Hazardous Wastes Listed by RCRA in the Federal Register on May 19, 1980 (See Footnotes for explanation of symbols used) 234 Table D-5. (Continued) £ a M mi 3 C h a a Se i - 3 82 ? Isjs- *? - s"3 J. J--H 3§ si**- JJ! • & *• u> • J.15^ sa ‘■8 H i 1^3}*- ** f,r: f I sis its zi •".ala .s me u m 9 l«^n ;«3*si a -h p-t *4 *4 *4 •> 4 M lw •■« U U •■* O SiJ8•. • C • ** «M U Wi • UOJ 2 i i * 1**1 nip 1:. s *« t-U 3 « — o • S *5 2 IS - 85 -. 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K w u oa il* i.| lii a< ■ = s i ill •:* Jij s :r r-a }? id -4.M I-4X » • * • -2-. • 4* 0 j^u -.?£ - X M ►—OK lao 332— 8- S 2 — ® i 3 ^ -T 3 X ai44UO 4 U 4. C *4 O. U 236 Table D-5. (Continued) 237 Table D-5. (Continued) 238 Table D-5. (Continued) A e it i a t £ | 8 a a a a a a a ll {11 i - k k a u k o oak ** 1 'll 5 1 \i\ i\\ 1* = I*i 1*-* s 1 l l! Is! i llfj HH - ! li§ i. ? «; it; j s{ S its its 5 : 28lg 28S1 2*Il 3-: 3 111 ill 3 1 Jill ill sill i !| u ** ft ° s a* ief. it kit!. it je 5. as is! . 1 ! 1 9 -5— • • I — • - • — • •••*«*£ £ «X4>w)ap • • • •*- Is 5 = i§ 22 8-ig 22 3 = i8 22 S=jg S £ £ :: ““s;-® ““i^ 8 , ■* -s |I £35*- .° ?3i- -° Z32~ -• 23.!~ -° 2 «C S?.°*.2 8 8 V > S>b-? Sku.k i » b . • ■ k b • g m rs -a 33 ssjjs 5 ssjjss 8 ssiis 3 sriis 1 s » s • 4* ■ v • ** 3 8 s * ? 2 X j? n fills -s -s 8 o &&J! j 8 .£ •* u u X — 4 *“* 7 X 0 0 U * “ _ 0 ** _ X X fc. 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(Continued) 2 2 2 2 8 » M M -J -J h j *! i * 0. * 0» * a a * *t ! h\ w 0 *•£ I|1 f- ill 5* V J u m « o 3 *a • *» ‘ S-? •g 1 • 0 0 9 •• l> m m a B 0 *0 «4 «« ■3 44 0 0 0 iIs s a! is is - ifj : 1 is: 1 *85* <4 « 0 -4 4 * « • 4 * 4 « 0 *. 6 4J *4 C *. 0 *4 *4 6 w • M 1 = ] J*] = j S* 13 J 5 -51 a s ii * s- si £ 111 "111 1 "111 l - S 3 3 2 " S " -3 JSS'J 1 ill •iili • til• 5 8 5 8 j 835 8 i |85 8 1 a • u — «- a * k — — a a J U 11 If* I g - S Ji 0 U • 0 W B - • M & b • 3 ih •! L £ . iftle a ==2e 3 =- tj •* h 2 0 m •• 0 2 0 ►* •- *- m w a — k « «- p • b m* • 1- *- *■# • P - a .a gf ■ .j 8 ► * u a* 4 w 0 a *4 *409*4 2 3 3iii 0 * u 0 — 0 • b M M 0 • M *4 u X Tl 0 * 4 i! 4 - w X • X wCnAiU mUm0u aui •• J 1 ii 55 Sil - - 31 :j. 8^5 5 5 -3 1 ';jjl i i s :85 u 3 a a 3 a * — «H -J <4 8 5 1 551 3 a Sj - 2 it a- 5 s : s :: [s r» j S | • as 2 J 4 40C N«#h H “1 0 W J • w *4 • «4 • ** £ 8 ! 8 13 M 0 *• (J « W 2 J S a * 1 J 1 1 I 1 1 1 1 1 i i *4 *4 _* la 5 L 3 , jk U >* o**»0 0 A -o J3 •* f (4 0 - 8 3 -:i«i • l» a * a 5-3«{ 3 | 3 -.iiKs •S; £2 £ -T5 2 --S • U 0 *# 0 0 t* 5 i urn m S,1 1 4 »a H * 0 : s j t* « m r> r> ^ m n « n n r% m i* 0. *4 0< ^ ^ r> <0 ^ ^ 'g n n M A • n n n n N • •• ■ ^ •# •0 §« & *- B 0 0. w i 1 s *9 8 1 0 S2 •>« X C Sill • 1 i • i * 1 : - r f 8 c , ~ sji’i h i il> lifii !ll*.l{t - s 3 - i *4 « a. 0 *4 i £ > B *# u « o g 6 &w*qC0 0 *9 * u - t» C 0u I c » j • • a 0 «■ 04 a *# 9*4 •* -# •3 o «• $ «-• 0 k. t u 4 n 0 ^ u -q A. *4 * M i Q ^0 • i 1 km y S u o * 4 . ►* 00 v ■ ^ m «* #5*5* u«L B a • *0 *0 f -* 0 « *400 ~ T9 r = , :1: i i »Ji j« - 3OC0U0 ->*.2*4*4 —. *4 u «4 00 tft 0 0 *. a. 4 - tn o 0 A M M 0 (k*# 0*4 js i3 a ; J 8 ■ -1 3511 5 : a 1 5 • * - ss.^U^H^IS j g S §? 5 *5 J 5 SI j 3 J? 25 UH W|4>i W« 2 « 0 •* *1*4 I * f 0 0 0 W 0 0 U *# 0 6 m CL U ll 0 3 *4 »4 0 <4 A* 0 X m m *4X 0 *4*4 ll 511 si 1 ! iiU si- L, u 0*40 <4 1 . 0 W •* L • u. 0. 2 « <4 Q 9 0 M A M 1* O «*4 *4 241 Table D-5. (Continued) 242 Table D-6. Applicability of Available Incineration Processes to Incineration of Hazardous Waste by Type id l 03 c •H O c •H o u 4* ■h jc a 4-3 •H Li *j m iH 43 3 .c x TJ 43 N •H4J TJ TJ •H 43 3 XX c o TJ H ■H 4J &SJ •H -n -J C >« L. C 43 >—I 4-> -H o j* OS x x X X X X X X X X X X w X X X TJ X X X X X X X X X X X X 43 41 X X X CP X X TJ c >i a c TJ 43 -V c 43 VI o o 43 o JC 3 rH 43 G 43 4-> 4J V) 4-3 4-3 3 JC 4-3 43 CP v> i—4 r—4 3 •H •H JD O' <4-1 CP V) TJ -H 43 43 TJ o 3 4-3 C o O TJ 3 V) •H E 43 41 VJ - 43 c i—4 c g i—4 >4 Li 4-1 4) C 4-> V) c 41 TJ 43 - 43 3 3 V) r-4 43 43 C & 41 >i • c T) o CP 43 Li V3 xc o E o 4-3 XX 43 O' J< u •H c u L. >—4 4-* 43 *3 a •H U Li 43 VJ •L3 O i—1 4-» O ^-Vi 3 43 VI 4-1 TJ V) E c -r4 >4 E c 43 g 3 1> a • o JC rH Li V) •H •• c o •H c a 43 Li 43 o -Q u a If) o U 43 & w •H u E 43 43 U a 4-> JC •» O' 4-1 43 * a *H > TJ 43 CP Li CP V) - l/l c 41 TJ r—3 43 c -i-4 •H 4-3 (J bu Li o Li i—4 >i 43 - Li 4J •H u 43 43 43 > 43 V) r—4 & c •H 0 O <44 43 43 r—I » Li 43 11 4-3 - H Li •H CP 3 o 4-3 O r—4 *H Li 43 iH rH r—H V) u a 4) L, u Li O U u •H u 43 O V) 43 U 4) i—3 3 rH 43 Li •H a 43 •H •• o 43 -H •H rH g CM 3 r-4 V) 43 a •• 3 &> fO E 43 c V) 43 4-3 c VI 3 K c 43 o - o JQ 43 4J o w C 43 a 4-3 43 3 Li 43 • • 43 T3 •§» CP O 4J 4-3 Li CM 43 <3 i—4 43 Li TJ 43 Li 3 ’—-- CP U-l a. E V) CP •H 43 4-3 CP V3 43 ■—- & 4-3 TJ s a *H Li Li O Li c 43 Li P •H Li •H 43 •H C rH O ►H i-J O 3) W O & X O rH » < 3 4) <44 <4-4 O 43 •H o to X M M m O ui 43 JC U TJ V) 43 • f-4 CP N G N •r4 O >1 G Li T3 C O C •r4 O 4-1 a u 3 4) •i— > c JC •H u •H TJ 4-> •r-4 V) S’ 43 -H r-4 U >i 43 Li XX 43 ■H 4-3 i—4 o -i-4 G 5 VI 4J 43 O JC T3 4-3 •H 43 3 4-3 V) TJ 43 43 • » a TJ a •H TJ -r-4 S’ S’ •H 43 TJ -r-4 43 rH > o <4-4 <4-1 Li 3—4 43 3-t <4-1 c o •*-4 4-3 43 Li VI •H w 43 JQ TJ 4) 4-1 •H .5 (0 TJ 43 TJ C 43 Li O 4-3 43 i_ 43 C •rH o c •H 4) -C 4-3 oo a> C a3 C/3 c o s (13 CJ l-i 3 O C/3 243 Table D-7. Compilation of HWDMS Data 3 Type of hazardous waste facility Number of facilities by EPA Region I II III Facilities that store or treat H.W., but have other processes 756 1348 907 Facilities that only store or treat H.W. 536 1015 641 Facilities that incin¬ erate H.W. 54 73 76 Facilities that treat or store H.W. in surface impoundments 89 122 107 Facilities that dispose of H.W. by: Landfill 35 49 57 Injection Well 5 10 1 Surface Impoundment 24 15 28 Land Application 4 11 6 Ocean Disposal 0 10 0 Disposal Total 68 95 92 IV V VI VII VIII IX X Total 1647 1974 1117 345 165 853 55 9167 1128 1419 668 248 88 650 44 6437 105 112 101 26 16 33 1 597 294 196 370 36 54 94 4 1366 94 90 124 11 32 36 3 531 12 25 85 5 3 5 0 151 73 37 115 15 15 34 4 360 50 29 62 12 20 26 1 221 1 0 1 0 0 4 0 16 230 181 387 43 71 105 8 1280 a Note that these numbers represent the number of valid applications which may not be equal to the number of sites currently in operation. Source: Anon. 1982, Hazardous Waste News. 244 Table 0-8. Industries Subject to Effluent Limitation Guidelines and Pretreatment Standards Industry Adhesives and sealants Aluminum forming Battery manufacturing Coil coating Copper forming Electric and electronic components Foundries Inorganic chemicals Iron and steel manufacturing Leather tanning and finishing Metal finishing Nonferrous metals Nonferrous metals forming Ore mining Organic chemicals, plastics, synthetic materials Pesticides Petroleum refining Pharmaceuticals Plastics molding and forming Porcelain enameling Pulp and paper Steam electric Textile mills Timber products processing 245 APPENDIX E AUXILIARY INFORMATION ON LANDFILLS AND LAND TREATMENT 247 * 1 - UJ 1— z O Ol o ro o C\J WH < C(J r—i CM oo C\J < 1/1 E J Jtu 3 W < 3 >— 3 5 — Cl Z O o o >—i cj o- 1 — 0 . -- O * * 3 * rH Cd cn cd VO z oc Oo i— uj uj —i to O cn o CO o o a) a t— t— c co rH CVJ LO f— 5 -i C QJ z Z< LO ro lo #> VO 00 00 00 {/) LU c CD LU > LU OO C C O LT) LO o o o o 1 CD LU O 0 oo oo rH cd QC U- QC LU LU O C Q_ c 0 ) ‘'O 6 cd c z o Q£ OlOr- Lul LU H O CO o LO LO rH >r _4 Q 5 — 1 — C O ^r o C\J oo LO Z > •—• 1 — 1 33 «✓> 0 » #» m* s < LO ro I— 3 r—i OJ CM CM w z: a. o c LJLLOO'r- e OCOQ.'-E •rH c o o 1 —» •H LlI 1 —■ 00 o o CO 4 -J 5 — < c- o o oo CO r-H cd e£ — 1 o CO 00 cn o OsJ rH 1 — => M A A * 0 OO CL rH LO oo CO Cu O rH o CL CO E3 Vw O C o eC Znj WOw z: — u * c L- L- C oo >> o L- z (D O CD •O 4 -> CL > •* ro E O L- -*-> L0 if) C if) QJ ro >v+-> rO r— 3 O >> oo 3 C Q c o d) cnx C O -C ro «T 5 >- •*-> CD O C /0 LU oo > cn< 4 — LO •r- _C ro 1 — LU c c c «/) u c -Q C o C H— L0 o u L- uo < o o o o o Q s- a> i— u •r- 3 rO CD o >> o z z z z CQ 3 : CO z c h— CQ CQ Z Z QC UO o c 249 U1 OT3 r—* in I— c c is) C ID h- CL Z O O —• h- CL C\J LT) cn LO 00 CTi co 00 LO CNJ 0k rH o LO •t •* CO cn z oc: otj LlJ LU i—• t/> o cn CsJ cn CO Q 1 — 1 — * * 0k < O 0 D 3 E Q_ Z r—4 *“H r—4 rH LlJ U- O *—< Od O Cl LU o C LU z: < >-h i/) lu i— c m U ^ < tn r-4 Cxi LU LU lu lu a: Q.O< o LO O O CNJ ^ a3 /“—s "O —i CO CNJ CO CNJ O (— *— CO CsJ o CSJ O z: —4 Cvl LO co CO CO h— CO CO co rH LU C 0k * h- -J rH o LO r-H C ZD h- CL OO o CL rH r—4 i w 03 < LO LO LD 1^ LO rt f_i —J _J z * 0k 0k 0k * •* 0 > 0k 0k oo ID CXI *3" CNJ r —4 CNJ r —4 r —4 CL o CL 03 in ■r— •r— z 4 -> U cn JZ JZ •r— -O •— O C LO CJ 03 c D CD D C 03 3 •r— 03 CO o u oo LU oo >>co 00 LO 4-> in ■o jO c c i— JD > c cn 03 o 21 f— LU CD U L •r— 00 03 03 (/) c o •r— CD E in 03 -C 03 •r— 4— oo c to cn 03 (D u c: U r— 4-> o 4 -> CJ > o C -r- 4 —> u u o z C- C £ 4-> u _£Z c •r— -U> L C. c c c o .C CD o _) r D -J Z CL HI ’"D _J CL CL >- C CJ CJ CJ CJ LU •—< oo CJ CL oc 03 •r- c CD 03 LU LO > in (— i- r— 03 •r— < CD >N C o 1— "D on 03 c OO c o •r— •r— S c ■r— TJ r— CD CD -C C r— Z CL o r —4 r —4 250 Michigan Detroit 4,446 Flint 517 Grand Rapids 553 6,215 9,098 2,883 100 2,883 9,098 Kalamazoo 261 Lansing 438 PERCENTAGE REMAINDER SMSAs TOTAL SMSA REMAINDER OF STATE OF STATE TOTAL STATE LOCATED IN SMSA POPULATION STATE OF STATE AREA IN POPULATION POPULATION STATE AN ESA POPULATION a IN ESAs a POPULATION POPULATION 3 ESAs IN ESAs a IN ESAs a lo LO CO C\J LO C\J o o ld CO o CO OsJ LO LO in o rH CO co 00 LO LO vO * r* #* co rH CO rH C\J i — C"- rH ro LO OsJ rH OsJ o o OsJ LO Osl 00 rH co OsJ r^ r^ co LO CO o CO CO C\J Osl LO e» w\ C\J T—i rH o CO o o o 00 CO CO o OsJ o LO o CO LO co OsJ Osl OsJ 1 — rH CO LO LO r-*. 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Z3 -Q C i — S- CO • f— •r— O • r— O O CD 03 CD 03 03 •r— 3 21 »—« 21 CO Z Q 51 3: > 251 West Virginia Huntington 291 291 1,791 1,500 67 1,005 < t— CO On •—» i/) (— c . ro o ro r -1 cm on cm o < x> I— cl z o o —* h- a. -3" ro oo <\j >—i cm cc lu uj Q r < oo I —• A A CVJ ro C\J rH fH rH UJ o < UJ Z C •— i/i lu I— C ro o oo o 00 ON □ 1— »— VO 00 ID 00 LD VO -3- z < < uo in 00 ID r-H ON O H|- J A A A A A A A A <003 ro rH CVJ CNJ CVJ CVJ CVJ CC O CL «3 o >—« CO CNJ O ON 1— LD 00 00 CM ID CVJ ID CVJ LU ro oo O ro r-H CO ro t— _J A A A A A A A A o rO r—• 4~> ~o -o o o r— •r— c •— to c oo LU CD O to ON JD > CD rO o ro “O u r— ON > rO •f— *r— > -C i— to oo c i. g i- -f— <_> z 1X3 0) r— r — «o ITS -r- U CD O • 0) O JZ 5^ o •O (_> 13 o o o z U_ -J Z o CL. 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J- 4-> 03 03 03 03 03 03 03 03 03 . p— 4-> • p> 4— CD 03 • r- -*-> 4-> 4—• 03 > > > > > 03 £ 03 03 o c o 4- J- o C c c — i < < < < < X X X to to UJ O (3 to L-H ►—« HH 259 Application-related geometric parameters _ _ Application-specific parameters (continued) c c C O o O OsJ X S- ■r- • r" • r - 03 c o 03 C 6 03 >> 4-> -4-> 4-> 03 C N o o> \ w o N 3 03 u o o o N 03 O o u- V4- V4- l_ r— 1- ZD • «* l/k to (/» U 0) ■O 03 Z •J -C c c c 03 CL T3 J »—i z «*-» 03 03 CL Q. •r— o -J HH c u 1- u CL 13 E £ Q 4-» 4-» =3 £ E X—X OJ 03 03 *w» • * 4-> X -*-> 4-> 03 -c: .C jC ^3 >> c C c -*-> -*-> 4-> • » 03 jO 03 4-» 03 C --- 4-> 03 C 03 4-> c 4-> Q 4-> .c c c c C o C U- 13 Q ZD E 3 c • r“ • I— O N o u- E r- \ c 1 -*-> C 03 -*-> c 03 -*-> c * N • r— • r- o fsl • r“ o c =3 u & < e \ N -X c •F” CJ +-> -*-> 4-> o to o *o N T3 03 *o E l/k UJ X D 3 l/> to 03 03 03 03 ZD 03 0 CJ P r— —1 r— r— 03 CJ •r* O • r— • • • r“ N “O < 0 »— E r— r— L. 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U 03 5 4-> O ^-x ^x • » u E D ni a. ‘i 03 Ql U c 4-» 1 1 0 • — • •» • A c 13 Q. Q. 8. 03 • » • * UJ C£. £ V—✓ -I \ CL ZD 4-> “O z X 0 ^~x < Q u 03 -*-> 13 \ 4-> s 13 03 cr 0- 2 1 -O x_^ 03 C \ L. c 0 r— • r- u. 2 • • 03 Q 03 03 03 03 \ f— r— X-' 4-> 03 c 03 XD -*-> r— 2 4-> u O CL x^x X_X c c o C U C ■O 0 c 03 CL CL 4-> 1 ID < OJ r—x o N o • r- "e O T3 0 2 03 c • • JD L X - ^ p E N N c*— O . r— 0 5 V4- 03 X L 03 r— • r— m. e * O to c Q- 03 Q. u rsj r— • r— r— u c c c c r— 8 Cl Q. 03 03 o . r— Si o 0 * O 0 « c 03 Q. D Q. Q. o to o — JQ 4-> •p" -Q 4-> 0 O X 03 O \ Q. E u to to to 4-> U c 4-> s_ c • r* 03 C \ 03 C O 03 03 1 03 03 03 -§ 03 4-> E O 03 \ u 4-> u r— L. c "O L) 4-> u -*-> 03 u P N r— "D L 03 03 TD 03 2 o 0J c 03 c L- -C C T3 T3 03 1— a. X 3 • r— u U 0 U u 0 4-> 0 03 r— T3 • r - i • r* CL • r- o 4-> 03 0 03 • r— (J c jC • r“ • r- E 0 o C ZD E 03 03 C ^“x 03 c 03 u O E *— to o U *o 03 1 >> -O 03 >> O 0 O to • o 03 03 03 o 03 • - 03 O 03 03 C V 4 - to • O • 03 u LZ -C JZ • r- fe 8 • r— U 0 • r* u X UJ X -C O) -*-> 4-» 4-> Q jQ U ID O O (J >» 03 Q. 0 Q. £ hxk 4-> -C Ql u- C4- V4- u- V«. u- < Cf. C 4 - U- V 4 - u- • f— u Q. U- Vfr- U- V4- o o O O O 0 ^ O O O ^-x O 0 X • r“ D O O O o 1 — 1 X3 .c -C -C jC O O JD O O 0 •* O 0 JQ C C O O O 03 4-> 4-> 4-> Q) • r* z 8 • ^ O -J O • r- • r* • r— • ^ 03 CL Ql CL CL -*-> 4-» C -*-> 4-> -*-> «— 00 03 4-» 4-> (. £ <8 £ 03 03 O 03 03 03 < 03 03 O < l_ X 03 03 03 < o cr CL N a: cr CL a: a: tO w Ll. Ql a: CC CL 260 ■O 3 C C o o CO I LU a; jQ 4-> 0 ) oo 05 *o o C O c “O QJ N o /—s • r" o 3 ZD N CsJ 4-> M C CD E 03 • r— r— L. D u u -*-> TD CD 2 CsJ N CsJ • r* • r“ • r“ c T) E 05 E r-» o 05 o O 0 3 Q Ql to o • u *i N • A \ 5 oo ■w* 05 z; 05 03 CsJ o 0 ) CD 13 C3 3 $- 03 oo -C JZ • A . A r— 05 TD 4-> S- 4-> -*-> z> 3 c >> C c hH HH > flj • r— • r— _J • A _J i- r— 03 05 p “O O o c A *4- > oo . r— L- c c • A .Q . A c a; > 03 • r— • r— ■O 0) ■O "O • r— • r— r— a oo oo cd c QJ CD <*- o c o C S- oo • r— > o “O T3 o N o .r— c u c CD oo oo u • r— • r— CD -O u U CL T3 2 r-— t_ o Q cd a> CL • r— O 0 2 Q. oo Q. a. 15 E r— s_ g 4-> 00 oo 03 . r— t- 03 c c c o O o 00 -*-> 4-> 00 oo □ • r— 4-> 4-> L- L. ZD £ 4-> O C o c 4-> 4-> QJ O • r— 03 -*-> Q -*-> Q 3 3 13 4-> t4- Q) oo U E £ Q. Cl a. XZ • r— 00 N oo C c c E >> 4-> S- r— oo CsJ oo ■NJ . r— • r— • r- r— o Q O E O E c <4- >4- $ r- a a 00 oo oo 03 o • r— \ N 00 00 to CL •O «<-» C7) +-> a> (2 !2 2 T3 TD CD C 3 c 3 £ E E Q> Q) oo 03 • • 03 • * r— l- L- 3 -»-> ZI 4-> —i T3 "O “O 03 . r— • r— 3 ^ 3 C c c o 3 >> •— Z r— z 03 03 03 •«-> 0“ CT r— t—i r— ►—1 05 05 05 O CD QJ c O is) o 1/5 • i~ • r— • r— z cr cn O Q_ Q_ s —' _ l —1 _1 03 -Q u ■O 261 Source: Bonazountas and Wagner 1981. Table E-4. Geographic Distribution, by Region and Waste Land Treatment Sites in the U.S. State, of Hazardous Region Regional Office Number of fac 1 1 111 es V 1 Dallas, Texas 38 IV Atlanta, Georgia 45 IX San Francisco, California 19 VIII Denver, Colorado 18 V Ch1cago, 1111nols 16 VII Kansas City, Missouri 15 X Seattle, Washington 12 11 New York City, New York 8 111 Philadelphia, Pennsylvania 7 1 Boston, Massachusetts 0 State or territory Number of facilities Texas 29 Cal 1 torn la 18 Louisiana 13 Oklahoma 11 Ohio 9 Al abama 8 Kansas 8 Washington 8 Florida 7 Georg 1 a 7 Mississippi 7 Montana 6 North CarolIna 6 Wyoming 6 South Carolina 5 Mlssour1 4 Puerto Rico 4 Colorado 3 II11 no 1s 3 Kentucky 3 New Mexico 3 Utah 3 Arkansas 2 Indiana 2 Iowa 2 New Jersey 2 Mary 1 and 2 Minnesota 2 PennsyIvan 1 a 2 Tennessee 2 Virginia 2 Alaska 1 Oe1 aware 1 Guam 1 Idaho 1 Michigan 1 Nebraska 1 262 Table E-4. (Continued) Star# or territory Number of foe 11 1 111es New York 1 Oregon 1 Virgin Islands 1 American Samoa 0 Ar1 zona 0 Commonwealth of the Northern Marianas 0 Connecticut 0 District of Columbia 0 Hawai1 0 Maine 0 Massachusetts 0 Nevada 0 New Hampshire 0 North Dakota 0 Rhode Island 0 South Dakota 0 Vermont 0 West Virginia 0 Wisconsin 0 Source: USEPA 1983a. 263 Table E-5. Industrial Classification and Location of Hazardous Waste Land Treatment Facilities SIC Code Region State Landfarm Facl11ty 025 Pou1 try Feed IV Tennessee Arapahoe Chemicals Inc. 1321 Natural Gas Proc. VI Louis 1 ana Gulf Oil Corp. 1389 011 4 Gas ServIces IX Cal 1fornla IT Corp. - Benson Ridge Facility 203 Fruit Processing IV Florida Ben Hill Griffin, Inc. IV Florida Hoily Hill Fruit Products Co. IV FI or 1 da Orange Co. of Florida, Inc. 2067 Chewing Gum Manu. IV Georg 1 a Wm. Wrlgley, Jr. Co. 222 Weaving Mills, Synthetics 11 1 Mary land Tenneco Chemicals, Inc. IV Georg 1 a Southern Mills Inc. Senola Olv. 229 Ml sc. Textile Goods IV North Carol 1na Flnetex Inc. - Southern Olv. IV South Carol 1na Sandoz Inc. Martin Works 249 Mlsc. Wood Products IV North Carol 1na U.S. Industries, Inc. 2491 Wood Preserving IV Alabama Brown Wood Preserving Co., Inc. IV Alabama T. R. Miller Co., Inc. IV Mississippi Coppers IV Mississippi Pear 1 River Wood Preserving Corp. VI Texas Kerr-McGee Chemical Corp. V 1 1 Missouri Kerr-McGee Chemical Corp. 2600 Paper 4 Allied Products X Wash 1ngton Bolse Cascade/Paper Group 2611 Pulp Mills V Mich 1gan Simpson Paper Co. 2621 Paper Mills V Miss 1ss1pp1 Simpson Paper Co. 2819 Industrial Inorganic VI Louisiana Texaco USA (Dlv. of Texaco Inc.) Chem1ca1s VI Texas American Petroflna Co. of Texas 4 Cosden 011 4 Chemical 2821 Plastics, Materials 4 Resins V 1 Louls1 ana Shell Oil Co. VI Texas Relchold Chemicals VI Texas Union Carbide Corp. 2834 Pharmaceutical Preparations IV Tennessee Arapahoe Chemicals Inc. 2851 Paints 4 Allied Products IV Georgia Glldden C4R Olv. of SCM Corp. VII Iowa Landfill Service Corp. IX Ca 11 forn1 a Envlrc mental Protection Corp. - Westslde Disposal Farm 2865 CyclIc Crudes 4 VI Arkansas Arkansas Eastman Co. 1ntermed1ates 2869 Industrial Organic Chemicals V 1 Arkansas Arkansas Eastman Co. VI Lou 1s1 ana Chevron Chemical Co. VI Lou 1s1 ana Exxon Co. USA Baton Rouge Refinery VI Ok 1ahoma Conoco Inc. Ponca City V 1 Texas Celanese Tract K 264 Table E-5. (Continued) SIC Cod* Region State Landfarm Facility 2869 Industrial Organic Chemicals , VI Texas Relchold Chemicals (continued) VI Texas Union Carbide Corp. VI 1 Mlssourl Syntax Agribusiness Inc. IX Cal 1fornla Shel1 011 Co. - Martinez Manu. Complex 2873 Nitrogenous Fertilizers VI Texas Comlnco American Inc. Camex Operations VII Iowa Chevron Chemical Co. VI 1 Mlssourl Atlas Powder Co., Atlas Plant 2874 Phosphatlc Fertilizers VI 1 Iowa Chevron Chemical Co. 2875 Fertilizers, Mixing Only IX Cal Ifornla Environmental Protection Corp. - Westslde Disposal Farm X WashIngton Phillips Pacific Chemical Co. 2879 Agricultural Chemicals IV Georgia Union Carbide Agricultural Co. Inc. 289 Mlsc. Chemical Products IV South Carol 1na Abco Industries Inc. IV South Carol 1na Carolina Eastman Co. (Dlv. of Eastman Kodak) 2892 Explosives IV Alabama Hercules, Inc. VII Missouri Atlas Powder Co., Atlas Plant 29 Petroleum Production IV Al abama Plantation Pipeline Co., H£ Facility IV Mississippi Plantation Pipeline Co. VI 1 Nebraska Offutt Air Force Base IX Cal 1fornla Union 011 Co. of CA - Santa Marla Ref 1nery 2911 Petroleum Refinery II New Jersey Exxon Refinery 11 New Jersey Texaco U.S.A. 11 Virgin Islands Hess Oil Virgin Islands Corp. 111 Delaware Getty Refining & Marketing Co. 111 Mary land Chevron U.S.A., Inc. 111 PennsyIvania Arco Petroleum Products Co. 111 Virginia Amoco 011 Co. 111 Virginia Hercules, Inc. IV Alabama Hunt Oil Co., Tuscaloosa Refinery IV Georgia Amoco 011 Co. Savannah Refinery IV Mlsslsslppl Amerada Hess Corp. IV Mississippi Rogers Rental & Landfill - Exxon V 111Inols Marathon 011 V Ind1 ana Indiana Farm Bureau Coop. Assoc. V Ind1 ana Rock Island Refining Corp. V Minnesota Koch Refinery V Ohio Fondessey Enterprise IF Sit* #2 V Ohio Fondessey Enterprise LF Site #3 V Ohio Fondessey Enterprise LF Site #4 V Ohio Gulf Oil Co. U.S. V Ohio Sunoco Ref 1nery V Ohio Standard 011 Co. V Ohio Standard Oil Co. (Ohio) 265 Table E-5. (Continued) SIC Oode 2911 Petroleum Ref Inery (continued) Rag Ion State Landfarm Feci 1Ity VI Arkansas Tosco Corp. VI Louisiana Cities Service Co. VI Louisiana Conoco Inc., Lake Charles Refinery VI Loulsi ana Exxon Co. U.S.A. Baton Rouge Refinery VI Louisiana Gulf 011 Co. - U.S. VI Loulsi ana Gulf Oil Corp. VI Louisiana Marathon Oil Co. LA Refining Dlv. VI Loulsi ana Murphy 011 Corp. VI Louisiana Plantation Pipeline Co. VI Louisiana Shell Oil Co, VI Louisiana Texaco U.S.A. (Dlv. of Texaco Inc.) VI New Max Ico Shel1 011 Co. Inc. VI Oklahoma Bas1n Ref 1n1ng Inc. VI Ok 1ahoma Champ 1 In Petroleum Co. VI Oklahoma Conoco Inc. Ponca City VI Ok 1ahoma Hudson Refinery VI Oklahoma Kerr-McGee Refinery Corp. VI Oklahoma Sun Petroleum Products Co. VI Oklahoma Texaco U.S.A. (Dlv. of Texaco Inc.) VI Ok 1ahoma Tosco Corp. - Duncan Refinery VI Oklahoma Vickers Petroleum Corp. VI Texas American Petroflna Co. of Texas A Cosden Oil A Chemical VI Texas Amoco 011 Co. Land Farm VI Texas Arco Petroleum Products Co. VI Texas Champ 1 In Petroleum Co. VI Texas Coastal States Petroleum Co. VI Texas Cosden 011 VI Texas C^own Central Petroleum Corp. V 1 Texas Exxon Co. - Baytown Refinery A Chemlca1 VI Texas Gulf Coast Waste Authority VI Texas Mobl1 011 Corp. VI Texas Phillips Petroleum VI Texas Shell Oil Co. Odessa Refinery VI Texas Slgmor Refining Co. VI Texas Southwestern Refining Co. Inc. VI Texas Sun Oil Co. of Pennsylvania VI Texas Sweeney Ref 1nery A Petrochem. Comp 1. VI Texas Texaco Inc. - Amarillo VI Texas Texaco Inc. - Pt. Arthur VI Texas Winston Refining Co. VI 1 Kan. is CRA, Inc. - Phi Mips burg VII Kansas CRA, Inc. - Coffeyvllle VI 1 Kansas Derby Ref In 1ng Co. VII Kansas Getty Refining A Marketing Co. VI 1 Kansas Kansas Industrial Waste Facility, Inc. V 1 1 Kansas Mobl1 011 Corp. VI 1 Kansas Pester Refining Co. VII Kansas Total Petroleum, Inc. VI 1 Missouri Amoco Oil Co., Sugar Creek Refinery 266 Table E-5. (Continued) SIC Cod* Region State Landfarm Facl11ty 2911 Petroleum Retlnery VII 1 Colorado Gory Ret InIng Co. (continued) VI 1 1 Montana Conoco Oil Retlnery VIII Montana Conoco Land tarm VI 1 1 Montana Exxon Billings Retlnery VI 11 Montana Farmers Union Central Exchange/Cenex VI 1 1 Montana Phil lips Great Falls VIII Utah Amoco 011 Co. SUC Tank Farm VIII Utah Husky Oil Co. ot Delaware VIII Utah Phillips Petroleum Woods Cross Retlnery VIII Wyoming Amoco Pipeline Tank Farm VI 1 1 Wyoming Husky Oil Co. ot Delaware VI II Wyom 1 ng Little America Retlnlng Co., Inc. VI 1 1 Wyoming SIncla 1r Oil Corp. VIII Wyoming Wyoming Retlnlng Co. IX CalItornla Chevron U.S.A. IX Ca1 I torn 1 a Environmental Protection Corp. - EastsIde Olsposal Farm IX Ca11 torn 1 a Environmental Protection Corp. - WestsIde Disposal Farm IX Cal 1 torn la IT Corp. - Benicia IX Ca11 torn 1 a IT Corp. - Martinez IX Ca11 torn I a IT Corp. - Montezuma Hills IX Ca11 torn 1 a IT Transportation Co. - Imperial IX Cal 1 torn la Shell Oil Co., Martinez Manu. Complex IX CalItornla Union Oil ot CalItornla X Oregon Chem-Secur 1 ty Systems, Inc. X Washington Arco Petroleum Products Co. X Wash 1ngton Mobl1 011 Corp. X Wash 1ngton Shel1 011 Co. X Wash 1ngton Texaco U.S.A. (Dlv. ot Texaco. Inc.) 2969 Ind. Organic Chemicals IX Ca 11 torn 1 a Environmental Protection Corp. - WestsIde Disposal Farm 3011 Pneumatic Tire Manu. VI Oklahoma Dayton Tire A Rubber Co. 3317 Steel Pipe A Tubing Manu. VI Texas Quanex Corp. Gu1t States Dlv. 3471 Plating A Polishing IV North Caro 11na Neuse River Wastewater Treatment Plant VII Iowa Landtl11 Service Corp. 348 Ordnance A Accessories IV Flor1 da 011n Corp. IV Kentucky Lexington - Blue Grass Depot Activity X Guam Anderson AFB X Idaho Omark Industries, Inc. 3483 Ammunition VI Texas Lone Star Army Ammunition Plant 349 Mlsc. Fabricated IV Alabama Reliable Metal Products, Inc. Metal Products VI New Mexico Olman Heath Co. 3496 Mlsc. Fabricated Wire IV Georg 1 a Gilbert A Bennett Manu. Corp. Products V 1 Texas Roman Wire Co. 267 Table E-5. (Continued) SIC Cod* Region State Landfan* Feel 1Ity 3498 Fabricated Pip* 4 Fittings IV Florida Armco, Inc. 3533 011 Flald Machinery VI Oklahoma Lee C. Moore Corp. 3589 Service Industry Machinery IV Georgia General Electric Co. IV South Carol 1na General Electric Co. 3621 Motors 4 Generators IV Mississippi American Bosch Electrical Products 3641 Electric Lamps IV North Carol 1na General Electric Co. 3662 Radio 4 TV Conmun1 cat Ion Equlpment IX Ca11forn1 a The Grass Valley Group, Inc. 3679 Electronic Components IV Florida Tropical Circuits, Inc. IX Cal 1fornla Hughes Research Laboratories 3743 Railroad Equipment IV Alabama Evans Transportation Co. 3999 Manufacturing Industries 11 New York Borden Chemical A4C (Division IV Kentucky Borden Chemical A4C IV Kentucky General Electric Co. 4441 Marin* Terminal VI Loulslana Conoco Inc., Lake Charles Refinery 4463 Marine Cargo Handling VI Louisiana Texaco U.S.A. (01v. of Texaco Inc.) 49 Geothermal Energy Production IX Cal 1fornla IT Corp. - Benicia IX Ca11forn1 a IT Corp. - Montezuma Hills IX Cal 1fornla IT Corp. - Martinez IX Cal 1forn1 a IT Transportation Co. - Imperial 4953 Refuse Systems 111 Pennsy Ivan 1 a G.R.O.W.S. Inc. Landfill V Ohio Cecos VI Loulslana Rollins Environmental Services VI Louisiana Shreveport Sludge Olsposal Facility VI Texas Gulf Coast Waste Disposal Authority VI Texas Waste Disposal Center IX Ca11forn1 a Casmalla Olsposal IX Cal 1fornla Chemical Waste Management, Inc. IX Cal 1fornla IT Corp. - Benson Ridge Facility IX Cal 1fornla M. P. Olsposal Co., Inc. IX Cal 1fornla Slml Valley Sanitary Landfill 4990 Refuse Collection 4 Olsposal IX Ca 11forn1 a Oakland Scavenger Co. 5171 Petroleum Terminal VI Loulslana Texaco U.S.A. (Dlv. of Texaco Inc.) 7694 Armature Rewind Shop VI 1 1 Montana General Electric Co. 7699 Repair 4 Related Services VIII Montana General Electric Co. 8221 Colleges 4 Universities VIII Colorado Colorado State University 268 Table E-5. (Continued) SIC Cod* Region State Landfarm Facility 9711 National Security IV Al abams Maxwel1 AFB IV Florida Tynda1 1 AFB IV North CarolIna XVIII Airborne Corps A Fort Bragg IV North Caro 11na Seymour Johnson AFB IV South CarolIna Shaw AFB IV Tennessee McGhee Tyson Air National Guard Base VI New Mexico Mhlt* Sands Missile Range VII1 Colorado 11.S. Army X MashIngton Yakima Firing Center Source: USEPA 1983a. 269 » 270 271 APPENDIX F AUXILIARY INFORMATION ON GROUNDWATER 273 Table F-1. Computerized Groundwater Data Bases Name Geographic coverage USGS contact/telephone number Ground Water Site Inventory (GWSI) Al1 of U. S. Kathy Hunt/703-860-6871 High Plains Regional Aquifer System Analysis (AQUIFERS) Colorado, Kansas, Nebraska, New Mexico, Oklahoma, South Dakota, Texas, Wyoming Richard Lucky/303-234-6017 Kansas Water Level File (KWL) a Kansas Jesse McNel11 s/913-843-0701 Annual Observation Well File (AOWF) New Mexico James Hudson/505-766-2011 New England District Ground Water Level Data Base (NEGWL) 3 Entire New England USGS District Robert Wakelee/617-223-2822 Northern High Plains File (NHP FILE) Northern High Plain Area of New Mexico John McLean/505-766-2810 Nebraska Registered Well File (NRWL) Nebraska Donald Sch11 d/402-471-5082 Nebraska Water Level File (NWLF) Nebraska Donald Sch11 d/402-471-5082 Hydrogeology Subfile (HY) Long Island, New York George Hawklns/516- 938- 8830 Mlmbres Basin (MB FILE) Mlmbres Basin, New Mexico John McLean/505-766-2810 Nevada Test Site and Vicinity Well Inventory (NTSWI) Part of Southern Nevada and nearby Californ 1 a Richard K. Waddell/303-234-2115 San Juan Development San Juan Basin in Northwest New Mexico Peter Frenzel/503-768-2810 Water Level Subfile (WL FILE) Long Island, New York George W. Hawkins/516-938-8830 a Data is Included In the GWSI. Source: USD I 1979. 275 Table F-2. Listing of State Geologists - 1983 a State Name & Title Address & Telephone No. A1abama A1aska Arizona Arkansas Cal i form' a Colorado Dr. Ernest A. Mancini State Geologist & Oil & Gas Board Supervisor (Ernie) Dr. Ross G. Schaff State Geologist (Ross) Dr. Larry D. Fellows State Geologist (Larry) Mr. Norman F. Williams Director (Bill) Dr. James F. Davis State Geologi st (Jim) Mr. John W. Rold Director & State Geologist (John) Geological Survey of Alabama P.0. Drawer 0 University, Alabama 35486 (205) 349-2852 FTS Direct Division of Geological and Geophysical Surveys 3001 Porcupine Drive Anchorage, Alaska 99501 (907) 274-9686 FTS Direct Bureau of Geology & Mineral - Technol ogy 845 N. Park Avenue Tucson, Arizona 85719 (602) 621-7906 FTS Direct Arkansas Geological Commission 3815 West Roosevelt Road Little Rock, Arkansas 72204 (501) 371-1488 FTS 740-5011 (Operator) Department of Conservation California Division of Mines & Geology 1416 Ninth Street, Room 1*341 Sacramento, California 95814 (916) 445-1923 FTS Direct Colorado Geological Survey 1313 Sherman Street Room 715 Denver, Colorado 80203 (303) 866-2611 FTS Direct 276 Table F-2. (Continued) State Connecticut Delaware Florida Georgia Hawaii Idaho II1inois Indiana Name & Title Address & Telephone No. Dr. Hugo F. Thomas Director & State Geologist (Hugo) Dr. Robert R. Jordan State Geologist (Bob) Mr. Charles W. Hendry, Jr. Chief (Bud) Dr. William H. McLemore State Geologi st (Bill) Mr. Robert T. Chuck Manager-Chief Engineer (Bob) Dr. Maynard M. Miller Chief (Maynard) Dr. Robert E. Bergstrom Chief (Bob) Dr. John B. Patton State Geol ogi st (John) 277 Department of Environmental Protection Natural Resources Center 165 Capitol Avenue, Room 553 Hartford, Connecticut 06106 (203) 566-3540 FTS Direct Delaware Geological Survey University of Delaware 101 Penny Hall Newark, Delaware 19711 (302) 738-2833 FTS Direct Bureau of Geology 903 West Tennessee Street Tallahassee, Florida 32304 (904) 488-4191 FTS Direct Georgia Geologic Survey, Rm. 400 19 Martin Luther King Drive, S.W. Atlanta, Georgia 30334 (404) 656-3214 FTS Direct Department of Land & Natural Resources Division of Water & Land Development P.0. Box 373 Honolulu, Hawaii 96809 (808) 548-7533 Bureau of Mines & Geology University of Idaho Campus Moscow, Idaho 83843 (208) 885-7991 FTS 554-1111 (Operator) Illinois State Geological Survey 615 East Peabody Drive, Room 121 Champaign,* Illinois 61820 (217) 344-1481 FTS Direct Indiana Geological Survey Department of Natural Resources 611 N. Walnut Grove Bloomington, Indiana 47405 (812) 335-2862 FTS Direct Table F-2. (Continued) State Name & Title Address & Telephone No. Iowa Kansas Kentucky Louisi ana Mai ne Mary!and Massachusetts Mr. Donald L. Koch Director A State Geologi st (Don) Iowa Geological Survey 123 North Capitol Iowa City, Iowa 52242 (319) 338-1173 FTS Direct Dr. William W. Hambleton Director & State Geologist (Bill) Dr. Donald C. Haney Director & State Geologist (Don) Dr. Charles G. Groat Director & State Geologist (Chip) Dr. Walter Anderson Director & State Geologist (Walt) Dr. Kenneth N. Weaver Director (Ken) Mr. Joseph A. Sinnott State Geologist (Joe) Kansas Geological Survey 1930 Avenue A, Campus West The University of Kansas Lawrence, Kansas 66044 (913) 864-3965 FTS Direct Kentucky Geological Survey University of Kentucky 311 Breckinridge Hall Lexington, Kentucky 40506 (606) 257-5863 FTS Direct Louisiana Geological Survey Department of Natural Resources Box G, University Station Baton Rouge, Louisiana 70893 (504) 342-6754 FTS Direct Maine Geological Survey Department of Conservation State House, Station 22 Augusta, Maine 04333 (207) 289-2801 FTS Direct Maryland Geological Survey The Rotunda 711 West 40th Street, Suite 440 Baltimore, Maryland 21211 (301) 338-7084 FTS 922-3311 (Operator) Department of Environmental Quality Engineering Division of Waterways - 1 Winter St., 7th FIoor Boston, Massachusetts 02108 (617) 292-5690 FTS Direct 278 Table F-2. (Continued) State Michigan Minnesota Mississippi Missouri Montana Nebraska Nevada Name & Title Mr. R. Thomas Segall State Geologist (Tom) Dr. Matt S. Walton Director (Matt) Mr. Alvin R. Bicker Director & State Geologist (Al) Dr. Wallace B. Howe Divisi on Director & State Geologist (Wally) Dr. Edward C. Bingler Director & State Geologist Mr. Vincent H. Dreeszen Director (Vince) Mr. John H. Schilling Director & State Geologist (John) Address & Telephone No. Geological Survey Division Michigan Department of Natural Resources Stevens T. Mason Building P.0. Box 30028 Lansing, Michigan 48909 (517) 373-1256 FTS Direct Minnesota Geological Survey 2642 University Avenue St. Paul, Minnesota 55114 (612) 373-3372 FTS Direct Mississippi Geological, Economi & Topographical Survey P.0. Box 5348 Jackson, Mississippi 39216 (601) 354-6228 FTS Direct Department of Natural Resources Division of Geology & Land Survey P.0. Box 250 Roll a, Missouri 65401 (314) 364-1752 FTS Direct Montana Bureau of Mines & Geology Montana College of Mineral Science & Technology Butte, Montana 59701 (406) 496-4181 FTS 585-5011 (Operator) Conservation & Survey Division The University of Nebraska Lincoln, Nebraska 68588 (402) 472-3471 FTS Direct Nevada Bureau of Mines & Geology University of Nevada Reno, Nevada 89557-0088 (702) 784-6691 FTS 598-6011 (Operator) 279 Table F-2. (Continued) State New Hampshire New Jersey New Mexico New York North Carolina North Dakota Ohio Name & Title Address & Telephone No. Dr. Robert I. Davis State Geologist (Bob) Mr. Frank Markewicz Acting State Geologist (Frank) Dr. Frank E. Kottlowski Director (Frank) Dr. Robert Fakundiny State Geologist & Chief (Bob) Mr. Stephen G. Conrad Director & State Geologist (Steve) Dr. Don L. Halvorson State Geologi st (Don) Mr. Horace R. Collins Division Chief & State Geologist (Buzz) Department of Resources & Economic Development 117 James Hall University of New Hampshire Durham, New Hampshire 03824 (603) 862-1216 FTS 834-7011 (Operator) New Jersey Geological Survey Division of Water Resources CN-029 Trenton, New Jersey 08625 (609) 292-2576 FTS Direct New Mexico Bureau of Mines & Mineral Resources Campus Station Socorro, New Mexico 87801 (505) 835-5420 FTS Direct New York State Geological Survey State Science Service, Room 3140 Cultural Education Center Albany, New York 12230 (518) 474-5816 FTS Direct Division of Land Resources Department of Natural Resources & Community Development P.0. Box 27687 Raleigh, North Carolina 27611 (919) 733-3833 FTS Direct North Dakota Geological Survey University Station, Box 8156-58202 Grand Forks, North Dakota 58201 (701) 777-2231 FTS 783-5771 (Operator) Ohio Division of Geological Survey Fountain Square Building B Columbus, Ohio 43224 (614) 265-6605 FTS Direct 280 Table F-2. (Continued) State Oklahoma Oregon Pennsylvania Rhode Island South Carolina South Dakota Tennessee Name & Title Address & Telephone No. Dr. Charles J. Mankin Director (Charlie) Dr. Donald A. Hull State Geologist (Don) Dr. Arthur A. Socolow State Geologi st (Art) Mr. Daniel W. Varin Chief Mr. Norman K. Olson State Geologist (Ole) Mr. Merlin J. Tipton State Geologist (Tip) Mr. Robert E. Hershey State Geologi st (Bob) 281 Oklahoma Geological Survey The University of Oklahoma 830 Van Vleet Oval, Rm. 163 Norman, Oklahoma 73019 (405) 325-3031 FTS 736-4011 (Operator) Department of Geology & Mineral Industries 1005 State Office Building Portland, Oregon 97201 (503) 229-5580 FTS Direct Bureau of Topographic & Geologic Survey Department of Environmental Resources P.0. Box 2357 Harrisburg, Pennsylvania 17120 (717) 787-2169 FTS Direct Statewide Planning Program 265 Melrose Street Providence, Rhode Island 02907 (401) 277-2656 South Carolina Geological Survey Harbison Forest Road Columbia, South Carolina 29210 (803) 758-6431 FTS Direct South Dakota Geological Survey Science Center University of South Dakota Vermillion, South Dakota 57069 (605) 624-4471 RS 782-7000 (Operator) Department* of Conservation Division of Geology 701 Broadway Nashville, Tennessee 37203 (615) 742-6691 FTS Direct Table F-2. (Continued) State Texas Utah Vermont Virginia Washington West Virginia Wisconsin Name & Title Address & Telephone No. Dr. W. L. Fisher Director (Bill) Ms. Genevieve Atwood Director (Genevieve) Dr. Charles A. Ratte State Geologist (Chuck) Dr. Robert C. Milici State Geol ogi st (Bob) Mr. Raymond Lasmanis State Geol ogi st & Supervisor Dr. Robert B. Erwin Director & State Geologist (Bob) Dr. Meredith E. Ostrom State Geologist & Director (Buzz) Bureau of Economic Geology The University of Texas at Austin University Station Box X Austin, Texas 78712 (512) 471-1534 FTS 729-4011 (Operator) Utah Geological & Mineral Survey 606 Black Hawk Way Salt Lake City, Utah 84108 (801) 581-6831 FTS Direct State Office Building Agency of Environmental Conservation Montpelier, Vermont 05602 (802) 828-3365 FTS Direct Virginia Division of Mineral Resources P.0. Box 3667 Charlottesville, Virginia 22903 (804) 293-5121 FTS 937-6011 (Operator) Division of Geology & Earth Resources Department of Natural Resources Olympia, Washington 98504 (206) 459-6372 FTS Direct West Virginia Geological & Economic Survey P.0. Box 879 Morgantown, West Virginia 26507 (304) 594-2331 FTS 923-1511 (Operator) Wisconsin Geological & Natural History Survey. University of Wisconsin Extension 1815 University Avenue Madison, Wisconsin 53705 (608) 262-1705 FTS Direct 282 Table F-2. (Continued) State Name & Title Address & Telephone No. Wyoming Puerto Rico Mr. Gary B. Glass State Geologist & Executive Director (Gary) Mr. Ramon M. Alonzo Geological Survey of Wyoming P.0. Box 3008 University Station Laramie, Wyoming 82071 (307) 742-2054, 766-2286 FTS 328-1110 (Operator) Servin'o Geologico de Puerto Rico Dept, de Recursos Naturales Apartado 5887 Puerta de Tierra San Juan, Puerto Rico 00906 (809) 723-2716 a Provided by the U.S. Geological Survey, Reston, Virginia. Figure F-l. Concentration of Wetlands in the U.S. 284 APPENDIX G AUXILIARY INFORMATION ON SURFACE IMPOUNDMENTS 285 V* <*4 03 03 4 -> 03 Q S S 'O c CO 00 •u A < M zn •u 3 QJ CO d) co CO < § I e 3 o (X E H d) O CO M-l M 3 CO 0) S ■u 01 pq e o •H 4-1 co tH <0 (/> c ro v £ C7> C CO ec Q. 4) 4-1 to AyO03JLV0 ON I N I Wy313Q UOJ S3NM3ainO 287 GUIDELINES FOR DETERMINING CATEGORY Table G-l. (Continued) Step 2. Rating of the Ground Water Availability Earth Mate ria 1 Category 1 1 1 1 1 1 Unconsolidated Gravel or sand Sand with £ 50$ C1 ay with < 50$ Rock clay sand Cavernous or Moderately to Si1ts tone, Consolidated Fractured Rock, We 11 Cemented Unfractured Rock Poorly Cemented Sands tone, Shale and other Sands tone, Fault Zones Fractured Shale Impervious Rock Representative Pe rmeabi1ity 2 in gpd/ft > 2 0.02 - 2 < 0.02 -A -6 -A -6 in cm/sec >10 10 -10 <10 RATING MATRIX Thickness > 30 6A be 2E of Saturated Zone 3"30 (Meters ) 5A 3C IE £3 3A 1C 0E a This table is provided so that the user will understand the relationship between SIA ratings (available in the SIA data base) and key earth material parameters. See text (Section 5) and Silka and Swearingen 1978, for more information. Source: Silka and Swearingen 1978. 288 Table G-2. Relation Between SIA Earth Material Categories and the Unified Soil Classification System Step 1 Earth Material Category (and Step 1 Designation) Unified Soi 1 C lassificat ion System Designation Permeabi1ity Range (cm/sec) Gravel (l) GW, GP Permeable Medium to Coarse Sand (l) SW, SP > 10“** cm/sec Fine to Very Fine Sand (II) SW, SP Sand with £15% Clay, Si It (1 1) CM, SM, SC Semi-permeable Sand with >15% but £50% Clay (IV) GM, SM, ML 10~* to 10 cm/sec Clay with <50% Sand (V) 0L, MH Relatively Imperme¬ able Clay (VI) CL, CH, OH < 10"° cm/sec a This table is provided so that the user will understand the relationship between SIA ratings (available in the SIA data base) and key earth material parameters. See text (Section 5) and Silka and Swearingen 1978, for more information. Source: Silka and Swearingen 1978. 289 APPENDIX H AUXILIARY INFORMATION ON POTWS 291 Exhibit H-l. Needs Survey This survey Is conducted annually by the Priority Needs Branch of the Office of Water Program Operations of EPA In order to comply with the provisions of Section 205(a) and 516(b)(2) of the Clean Water Act of 1977. This survey collects design and operating characteristics for all of the municipal sewage treatment facilities In the nation and stores the data In computer retrievable form. The following characteristics are available for each facility: • Scope of collection and treatment (e.g., wastewater collection only; wastewater collection, treatment, and sludge treatment onsite; handling, treatment, and disposal of sludge generated by other facilitates). • Resident and nonresident population served and population not receiving treatment. • Actual and designed dally flow (thousands of cubic meters per day). • Average dally domestic flow and average dally Industrial flow. • Level of treatment (preliminary, primary, secondary, etc.). • Treatment and disposal methods of the liquid line (e.g., trickling filter, land treatment of primary effluent, activated carbon). See Table H-8 In Appendix H for a list of all treatment parameters In the data base. • Treatment and disposal methods of the sludge line (e.g., aerobic digestion, compositing, Incineration - multiple hearth, landfill). See Table H-8 for a list of all treatment parameters In the data base. Data may be retrieved from the Needs Survey data base for all facilities In a given state, county, congressional district, Standard Metropolitan Statistical Area (SMSA), zip code, or sewage authority jurisdiction. The choice of geographic designators In an exposure assessment will depend on how detailed and accurate the study must be. In most retrievals, all of the bulleted parameters are desirable because they are Important pieces of Information for Stages III, IV, and V. One carefully planned retrieval can provide data for all three stages In one step. There Is no user's manual for this system, but the EPA staff In charge of Needs Survey retrievals has many program already written, several of which would serve the purpose of exposure assessments with little or no revision. For more details on the Needs Survey data base, see the latest annual technical report available from the EPA Office of Water Program Operations (Washington, D.C.). 293 Exhibit H-2. Industrial Facility Discharge File (IFD) This data base Is maintained by the Monitoring and Data Support Division (MDSD) of the Office of Water Regulations and Standards. The IFD file Is useful In estimating exposure from chemical substances In wastewater because It provides Information on the Industrial contributors to a given POTW. For each POTW, this data base will give the following for each Industrial contributor belonging to one of the 21 major Industrial categories listed In Table D-8: • NPDES number, If any • Facility name • SIC codes (two most Important codes) • Type of discharge • Flow (thousands of gallons per day). The data for all POTWs In a state, county, or river basin can be retrieved by requesting SIC Code 4952 (which pertains to POTWs). This type of retrieval can be a source of both site-specific and generic data. It may be useful In determining whether a new Industrial plant might discharge to a local POTW because It can verify whether the POTWs In the area accept Industrial waste. Because a comprehensive list of all contributing wastewaters can be obtained In this way for a particular POTW, this data base In the prime candidate for use In conjunction with a POTW model for exposure assessments. This data base In currently used as Input to the POTW model used by the MDSD (see Section 6.1). Another useful retrieval from the IFD file Is by SIC code of the Industry of Interest or for the geographic area of Interest. For each existing Industrial plant, this retrieval will give the following: • NPDES permit number of each receiving POTW • Total Indirect flow (thousands of gallons per day) • Indirect discharge type. These data will allow a direct estimate of wastewaters routed to Individual POTWs where site-specific Information Is desirable for existing Industrial plants. This retrieval will also be useful In situations where the Investigator Is confronted with the problem of trying to guess whether any effluent from a new Industrial plant will be routed to a local POTW, because a general picture of the current wastewater disposal practices of the Industry (and for the geographic area) can be obtained from the printout. The one drawback of the IFD data base Is that It Is only about 75 to 80% complete. 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UJ - A X X X o X X X X X -J a. X O o X - X 1 4. X -J ►— x x a IN UJ -J -J ►X X UJ 1 - UJ X •X o a a. u A X 1 X Z 1 a x cc u a -J X ■ Q X H- rj A >- 1 •> X X 1 X UJ 3 X m X -J Ul X •— X X X "> 3 3 X 3 3 U-l U-l X OJ 3 o Q> CM 3 3 JP 3 X > X 3 X X Q) -H X i—1 3 a) OJ OJ 3 Ml X 3 3 OJ Ul O 3 3 3 3 0 O 01 X > X OJ CM CM X 3 X X oi cn p> 3 X cn 3 3 Mi 01 X X 3 Ml X 3 3 3 .3 0) a Mi 3 3 O Mi » 3 3 X X X oi cn 3 O 3 X X 3 oj OJ u 3 3 3 X X 3 X cn co 3 3 X 5 oj x 00 0J 3 X 3 r-1 CM cn 3 3 3 3 X J3 X CM cn o X X X TJ 0) x CM 3 O X p£ a X Ml a 3 4-> X 3 o 3 3 0 00 3 cn 3 X X a a) 3 o X 01 cn <0 0J CO O cn CO 3 oj nj oj 3 X X 3 °*s O o 0) cn cn a) OJ CJ C 3 cO 0 ) oj X 3 X X 3 oq cm a x 3 O CD 308 X <0 cd a) u H Pn Jj cd x) 3 o u (1) in 4 ) f—\ .—. X) H \ JJ O' —i * J 0 J A CO JJ JJ JJ c c c 4) JO 4) U ■—l O 3 Jj CU in H 4) 4-1 OU 4J c 0 M 4) O' <0 Ll 4) > z < 4) 0) C C o o z z •— 00 on 00 o o o o o o o N X X) QJ > o o3 ti 0) o JJ 4) P-i I a z o A JJ c 4) 3 «J C 4) O' 10 u 4) > < © i" on o o OOOOOOOOONOO 00 JJ >4 4) x 4) XZ JJ 04 C 4) JJ 4 C 4) fl 0 jj JJ >4 Jj X 43 0 jC j= 4 0 XZ o 4 JJ XL C a >4 jj Li x E 43 O 43 f-J i N X 4) u 0 4) JJ u 0 •rH N >4 tn C CU C 41 rH C a> 0 Jj u C JJ c 4) 4) E JJ 4) x 4) i UJ 0 E- 4) 3 <0 4) m f-H rH 4) a >4 E 43 c o rj 4 <0 TJ Jj —i r—4 Jj Jj 3 E 4) 4 Li £ r— »-H o 1 JJ 4) *-H X X —4 4J E 4) 41 3 •rH <0 3 Jj X 0 u * >4 c Z 1 N >4 JJ JJ o c a o JC > o TJ E Jj a w rH jj JJ cn rH •H r— J= 4) 1 4 o x •-J -rJ 4) 4) CO 04 m e- H Eh z CO o Eh u CU Q 03 CQ a z CJ U V z Z X U 309 Table H-5. Footnotes 05 3 05 3 4J 3 3 H 4-1 3 d 3 >H d r-4 CU X iH •H O o > d» *■— 1 •H X) "O 3 •u d •H •H ct3 J-l 4-1 o w CO •H U j-i a toO Cu d 3 r-H •H 5-1 CU i — 1 O CU • 4-1 O £ 3 - 1 o 4.1 to 5-1 X) 3 4-1 00 3 3 o cO 3 4-1 O T—1 s 05 44 CO 4-1 3 3 Su •H JO (-1 3 CJ o PQ 3 •H 4-1 toO JO 4-1 3 |3 x) t-4 3 05 3 3 3 4-1 05 > ■H 5-i 3 3 O O cu o 3 X! 0) O 3 3 4-1 • X) 05 05 3 t-l rH 3 CO 0) 05 3 s > JO 3 •H O 05 4-1 • i-4 4-1 3 05 3 XI >H 05 4-1 > 05 3 CU 3 O 05 05 05 3 £ CO 05 05 i — 1 3 PQ Pd 3 a Pi c0 JO 3 3 S-i 3 4-1 05 £ to 3 3 a 05 jo 3 05 05 4 -> d •r4 3 T—1 3 3 3 3 •rH 3 3 g 3 •H X 3 O 3 3 3 CU 3 CU i-4 3 44 •5 3 > 3 O toO JO 3 3 3 3 Jn > i—1 3 3 3 toO 3 3 3 • •r4 •rl CN 3 44 00 3 ■H CT\ 3 3 ,—i £ toO •H 3 3 3 O 3 Pd 3 3 3 3 X i—1 3 • 3 CU O 3 3 JO -rl 44 3 £ 3 o •3 3 3 t—1 3 3 3 3 £ 3 PQ JO •H O £ i—1 *H 3 3 • • z 3 3 3 3 3 3 n 3 3 3 O 3 3 z hJ X O u X C/5 310 Table H-6. Median Percent Removals of Selected Pollutants Through POTW Treatment Process 3 x oo X 2 8 < 3 s 3 g o 8 < Q. 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X X P d 4-J CO eu G o X CO d G m P • d G X P o !n co X e G 4-1 4-1 X X d X X a* O qj a c5 X G X > X vO i—1 QJ *H X G d ai co 4-> X CO • G X --' x P o d co P G o O Q) X i—i X d fn 4-1 PM PU X co X X X QJ CO > > G QJ P G X o d G X p X g cO P cO X QJ d G X co d G P •* X P X X • •r*H QJ CO X e CO X s X X T3 p d o 4-J 5 d co G G CO X C co co X X X G 03 d x X 60 cO cO d P t-H X X a- d i—1 G i—i X Pp d X d P X >. co O X G 60 o co CD X Q) i—i 0-< i—1 C4 •H 60 d Pi g cti co H3 x X CO O d X X P CO e co o G G i—H • cO rC X CO •H CO cO CO X 4-J X G X 4-1 CO o •H cO d d X £ P X (D o cO d co X O - 4-J 4-1 co X Cfl d oo 03 X d X X U G X > QJ i—i a. d c G •H £2 •rH CO i—i co c d g fc—i 4-J CO o O G r—1 o X O CJ m a X X X 5 t) •rH X cO CO X 4-J G X P X G CJ X o G X x oJ p p cO G P X CO X || ii 11 II II II H u X CJ Pi PQ td C H 2 < <0 H o X G X 60 311 MNNnnnnnwN — 000 — 000 O — — O I I I 3 »-H CP r—I (1) O 4-) P-i W z o f—t X O u o H < Da 4J •H flu (A c cd -3 g X < *-• 4-1 3 3 4-) r— 1 O £ 3 £ Q W J h cDo (N N N (N »- n ♦ O' CD CD — U- (N — in m *- r- in ^4(N vo — ao ^ vo in in o •T' vo ^ ^ ^ -d O •H o Pu 4J rH •H 3 u cd d CU p S QJ a xd CO -H d d CU > •H CU d *H £ X3 PH " td X! 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Summary of Treatment and Slude Handling Processes - Numbers of Plants and Associated Flow - United States Totals 3 Treatment processes Total flow (thousands Number of plants b cubic meters per day) b Liquid line Pumping, raw wastewater b b Preliminary treatment - raw screen 8,996 110,935 Preliminary treatment - grit removal b 24,165 Preliminary treatment - comminutors b b Preliminary treatment - others 75 2,593 Scum removal b 22,674 Flow equalization basins 413 10,928 Preaeration 416 23,715 Primary sedimentation 5,301 102,657 Trickling filter - rock media 2,647 20,841 Trickling filter - plastic media 62 1,816 Trickling filter - redwood slats 40 905 Trickling filter - other media b 322 Activated sludge - conventional 2,917 75,001 Activated sludge - high rate 40 3,681 Activated sludge - contact stabilization 1,208 12,124 Activated sludge - extended aeration 1,977 5,665 Pure oxygen activated sludge 68 9,650 Bio-disc (rotating, biological filter) 179 1,910 Oxidation ditch using mechanical aerators 553 1,297 Clarification using turf settlers 42 414 Secondary clarification 1,647 13,813 Biological nitrification - separate stage 151 3,279 Biological nitrification - rod and nit. 274 5,168 Biological denitrification 24 498 Post aeration (reaeration) 561 8,550 Microstrainers - primary 28 2,514 Microstrainers - secondary 75 2,315 Sand filters 1,340 9,746 Mix-media filters (sand and coal) 230 8,328 Other filtrations 43 1,061 Activated carbon - granular 21 1,175 Activated carbon - powdered 5 341 Two stage lime treatment or raw wastewater 13 285 Two stage tertiary lime treatment 17 295 Single stage lime treatment of raw wastewater 25 749 Single stage tertiary lime treatment 53 1,605 Recarbonation 26 1,162 313 Table H-8. (Continued) Treatment processes Number of plants Total flow (thousands cubic meters per day) b Liquid line (continued) Neutralization 16 164 Alum addition to primary 73 2,989 Alum addition to secondary 262 6,302 Alum addition to separate stage tertiary 66 1,778 Ferri-chloride addition to primary 42 1,256 Ferri-chloride addition to secondary 165 4,496 Ferri-chloride addition to separate stage tertiary 31 352 Other chemical additions 89 4,214 Ion exchange 2 204 Breakpoint chlorination 10 203 Airmonia stripping 8 302 Dechlorination 182 2,628 Chlorination for disinfection 7,737 81,587 Ozonation for disinfection 22 1,107 Other disinfection 6 3,458 Land treatment of primary effluent 77 82 Land treatment of secondary effluent (30/30) 496 2,975 Land treatment of intermediate effluent 169 343 Stabilization ponds 5,665 12,609 Aerated lagoons 1,166 4,926 Outfall punping 260 11,874 Outfall diffuser 71 5,081 Effluent to other plants 12 231 Effluent outfall 12,636 109,496 Other treatment 539 6,278 Recalcination 29 2,399 Sludge handling methods Aerobic digestion - air 2,960 17,823 Aerobic digestion - oxygen 46 608 Composting 16 2,907 Anaerobic digestion 4,286 78,701 Sludge lagoons 604 14,550 Heat treatment 163 12,999 Chlorine oxidation of sludge (purifax) 36 1,515 Lime stabilization 65 3,011 Wet air oxidation 51 3,172 Air drying 6,688 49,724 314 Table H-8. (Continued) •S* Treatment processes Number of plants Total flow (thousands cubic meters per day) b Sludqe handlinq methods (continued) Dewatering - mechanical - vacuum filter 1,115 51,460 Dewatering - mechanical - centrifuge 209 12,931 Dewatering - mechanical - filter press 102 3,657 Dewatering - others 29 1,748 Gravity thickening 709 38,864 Air flotation thickening 199 15,020 Incineration - multiple hearth 306 26,599 Incineration - fluidized beds 19 1,249 Incineration - rotary kiln 8 236 Incineration - others 13 1,075 Pyrolsis 2 97 Co-incineration with solid waste 5 140 Co-pyrolysis with solid waste 6 14 Co-incineration - others 0 0 Landfi11 5,918 66,930 Landspreading of liquid sludge 1,178 11,536 Landspreading of thickened sludge 925 15,514 Trenching 8 1,247 Ocean dumping 49 11,699 Other sludge handling 260 12,574 Digest gas utilization factilities 186 10,664 Miscellaneous Control/lab, maintenance buildings 8,204 100,540 Fully automated using digital control 40 6,463 Fully automated using analog controls 77 5,029 Semi automated plant 10,476 108,381 Manually operated and controlled plant 4,398 8,894 Package plant 1,724 1,882 Semi-package plant 1,945 6,608 Custom boilt plant 11,201 119,439 Imhoff tanks 318 327 Septic tanks b 13 Electrodialysis 0 0 Reverse osmosis 0 0 Pressure filters 3 28 Seepage lagoons 321 78 Rock filters 1 0 Polymer addition to liquid stream 9 954 Polymer addition to sludge stream 8 b 315 Table H-8. (Footnotes)) a Table H-8 summarizes the inventory of unit processes that was compiled during the 1980 Needs Survey, including liquid line, sludge line, and miscellaneous processes and types of controls. In each category the total number of processes is listed along with an associated total flow. The total flow was compiled using the present design flow of the treatment facility using the process. A unit process is defined to mean the complete process. For instance, activated sludge includes the aeration basin, associated blowers and other integral mechanical equipment, and the secondary clarifier, which is not listed separately. Multiple or parallel processes are counted as one process for any single facility. For example, if a facility has four aerobic digesters, the number of aerobic digesters counted in ths summary is one, not four. Therefore, the Number column denotes the number of plants using that rocess. ^Numbers in original document were illegible. 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CD v+- C u UJ C to E u to u 8 X o • r" to • r— UJ 05 t/5 • r - 4-> 3 * • r“ -*-> to > U > u n +-> L. UJ l/> • • • r~ • c to • ■> ro rO z 1/5 >» > L. LU 1 u >> 2*. U Q. z o L_ *4- 05 L. O LU u • r- 05 X >> u >> • r> s _ i h- CJ CJ to v_> XI CL Q CJ o > c to O 05 to L- .t; -8 cj c a> • x >> -*-> -O c c O rtf 8 c to od l. 05 to c L- 05 rQ 0) ro 05 •*” *— E *— "O to *— E — C 05 TJ 5 >0 > * £ -J CJ 330 Nashville Mass burning in waterwall incinerator Steam for urban heating 530 (processing 400) Nashville Thermal Transfer and cooling Corp. I.C. Thomasson 4 Assoc. Inc. (designer) T3 03 3 C I ►H 0) 5 >> ■3 S’ «. u 8. 03 CL to <3 8 O :d i >> u 03 > O u > oo u 0) c *o c 03 t> t> 03 u O “O c C 03 03 Q. • r— c u o — •r- 4 -» 4-> U 03 G U Ql O 0) 4-> tO no t- 0) c u c u 03 C7) c c L. 3 -O to l/> O. & • L. tO V 4 - 03 X X ^ 03 to C o 0) to CL C - o r— 0) O U ^ O •*- 03 -*-> > to 03 -*-> 03 C3 U 03 -M l_ to U L. 03 (D Q X S- O 0) t- co CM 03 ■4—> to u O 4-> 03 t. 03 C • r- u c u 03 3 T3 O) c • r“ c u 3 -Q to to £ to c O to O • to 0) 4-> 4-» 03 L. — 0 Ql X ^4- 03 CD — Q- <8 £ U < -*-» to c £3 >> -Q U L. 03 03 to 03 u a: o s£ 1 03 C 03 4-> 03 4-> CO —1 to 03 03 c S- 3 03 +-> 03 C7> C 3 -D to to U i_ 03 < - C "O O) to 03 to • »r- )D LL T3 03 ^ *— • • >> C70 S- 03 C 03 03 < O to < -c 4-> oo 3 c c CD 03 c z o £ §*. HH fU • 03 03 03 U • U *■ o X O X U_ r -5 u 03 “O 3 JD O *3* C U 3 -Q to to 1 331 Norfolk Mass burning in waterwall furnace Steam for use by 360 (two 180 tpd (Norfold Naval Station) facilities at Norfolk boilers operated U.S. Navy (owner), Public Naval Station alternately) Works Center, Norfolk Naval Shipyard (operator) Materials and Energy Recovery Facilities >> -3 $ «_ u 8. 03 CL ID 03 C O O CD 4-> U "S u Q. C/> to 05 U O U Q. ■o s T3 4-> Q. 03 ■P u 05 ^ O Q. >» CO O — 05 8 uT "no -*-» U C w O s_ •— <15 O •*- 4-* o »— '— -O 03 t/i 0 ) o 03 >> -Q 05 to D T5 L. t- 03 O >> ^ Q. m 0) to 4-> in 03 03 2 CD 4-> 03 2 cd c • r* c L. 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I • r* 4-> P o J— >> 05 < c U 05 c 05 05 4-> L. 14- 4-> CD JZ • r- 03 C rt) CJ> >> E 05 05 -*-* u 4-> 'D U 4-» 05 c 03 Ql 05 >> U Q. u o u O 05 3 CJ c CJ CD C •r* 4-» O o z o uo C o • r“ 4 • r - C • r— fTJ jC • r* —i a. s —' Ql UJ in > cc 05 fc in in o 05 4-> to CD C c u 3 JD to to £ in id to o o u u CD & oc c o cJ to to c 05 O C5 05 u u 03 05 CL CD • to cd C CJ *D 4-» L- CD -C 05 in E u o 4-> 0> 05 C II g u 05 CD ^ C C U UJ 05 c CJ z CD CD X § >» •r- tO m 3 U -♦-> 03 •»“ »- CJ 332 Madison Shredding, magnetic separation, RDF burned by utility 400 (max) (250 being City and M.L. Smith tronmel screening, secondary for electricity generation processed) Environmental (designer), shredding, ferrous metals ferrous metals Madison Gas & Electric Co. (RDF user) T> ) >> 4-> i- u g. 8 0J >X> CL to r— 3 8 4-> W (D r~ 03 4-> >> 03 4-> E •r* ID • r- 3 CD 4-> ■o O 4-> 3 c c U u >» 03 “D -Q <4- O • r- U T3 03 4-> O p> U- c L. 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C 03 • r* 03 4-> CD >> u "O • r* 3 4-> c C 03 CD 5 • f • r— 03 n 03 o uo s_-^ TD 333 UJ g 3 c cn 8 0) O L. CD 3 CO r“ 4-> 3 z c c UJ (/» a> < JO HH o L C 03 to • r— x c 1—1 l/> CO +■> o o r— CO > XI z • r— z u z 03 • ^ •4~> UJ xi Q. Q r— •—1 ?5 f— X S- z i/> j u o -4-> o O. o £ o Z ro 5 QC 3 X 03 CO f CL UJ z £ UJ CO 1—t CL ►—« >> *— > > 3 4-> CO c 3 C o -*-> c ?8 C =3 C 3 >> >> 3 4-> ^-s c co 8 • r- 3 c C I r- >> 3 3 >> c 4-» >- UJ 8 M a> 3 O 3 o 3 -*-> z •*- 8 o> 3 -X 03 03 O go +-> r— CO X i/i U o c ' L. rO u a> a> • r- ac c • r- a> g O O dj L o 03 L C u UJ 03 o C c »— Q. JZ P 03 >- 3 03 •— 03 r? 3 03 o >- >> •r- 4-> n 4-> c 4-> XI X K • 3 03 JO X 3 Q 4-> 2 o co co 3 03 4-> •r- U c 3 03 CO < JV 03 c >> rg - 8 >> u 0 > > o u (U cr 0 ) u L. 3 o = 1-8 O no QJ O C >■> r— t-i •>- 3 O g 00 *- c 3 8 co QJ c a> CO c u X -o >> -o 03 o ►— r— 4-> S UJ 03 • r* 03 x XI C3 CO < o co 03 03 >- .c o 3 ►— 3 t— * V4- < C 3 03 03 5 c O) o 03 CtL co 3 o> i—i c O' o O U O c co CL 8 03 O c CD 03 3 3 3 c < +-> • r“ UJ CO —j • r— & > < JD h- *o >- • r» co u z • co c u 03 i 3 Z 03 u co O CL z 4-> co 03 -*-> CL UJ CO O Q UJ CL CL i CO CO »—1 CO h-4 CO CO C3 »—« £ z z 03 c 0) l/» u < 03 c o c =3 3 U u 03 C -*-> 03 c c l/» U 8 3 <7> 3 03 8 03 3 CL O c O • Q U 03 XI c 03 P l/> U CD o 03 H 4-> • r“ h- 4-> 3 c < u c U 8> u 8 c o < T— HH >» 03 03 • r- c 3 03 u z 03 03 03 CO X cu 03 L O 8 > 03 8 r- 03 C GO • r“ u h- o N < • • £ ■*-> -X 03 -X -8 XI 4-> CO X xz o u- JZ Q co 03 co JX U- 03 CD 4-> c 03 X 4-» 4-> HH r— U CO c 03 *—t l- U (_ C u • r— c c r— z L 3 8 »— L < 3 8 _i 03 3 03 o o o 03 03 x: 03 O • p> 3 —1 < X 5 < CO UJ C3 —J z CO CO 3 o X CO —i X X O co O) 03 03 3 3 >> u 03 CD CO co >> 03 > u 3 CO 03 a> < 03 334 Table 1-2. Inventory of Small Municipal Incinerators No. of Capacity/Unit Year of Heat Manufacturer Units Location kg/day (tons/day) Installation Recovery U.S. Smelting (Farrier, 2 Crossville, TN 27,215 (30) 76 Yes Saokatrol) Halley 1 Nottingham, NH 8,165 (9) 75 No 1 Candle, NH 12,701 (14) 76 No 1 Bridgewater, NH 12,701 (14) 76 No 2 Meredith, NH 12,701 (14) 76 No 1 Canterbury, NH 8,165 (9 77 No 1 Pittsfield, NH 12,701 (14) 77 No 2 Kittery, ME 21,772 (24) 77 No 1 Harpsweil, ME 12,701 (14) 77 No 1 Auburn, NH 12,701 (14) 78 No Consumat 2 Stuttgart, Ark. 27,215 (30) 72 No 1 Augusta, Ark. 19,958 (22) 72 No 2 Tahlequah, OK 27,215 (30) 72 No 1 Donaldsonvilie, LA 27,215 (30) 72 No 2 Rayne, LA 27,215 (30) 73 No 2 Plaqueaine, LA 27,215 (30) 73 No 1 Kensett, AR 14,515 (16) 73 No 1 Skaneateles, NY Osceola, AR 27,215 (30) 73 No 2 27,215 (30) 74 No 1 Cleveland, OK 19,958 (22) 74 No 2 Pahokee, FL 19,958 (22) 74 No • * ' 8 Orlando, FL 27,215 (30) 74 No ' 1 Refugio, TX 19,958 (22) 74 No 8 Bellingham, WA 11,793 03) 74 No 3 Terrell, TX 16,329 (18) 75 No ' 8 Hot Springs, AR 27,215 (30) 75 No 2 Bentonville, AR 27,215 (30) 75 No 2 Hope, AR 27,215 (30) 75 No 2 SI loam Springs, AR 19,958 (22) 75 Yes 4 Blytheville, AR 16,329 (18) 75 Yes 2 Wrlghtsville Beach, NC 27,215 (30) 77 No 2 Tahlequah, OK 27,215 (30) 77 No 1 County of Coos, OR 27,215 (30) 77 No 4 North Little Rock, AR 22,679 (25) 77 No 4 Port Orange, FL 27,215 (30) 78 No 1 Atkins, AR 15,422 (17) 78 No 1 Wilton, NH 27,215 (30) 78 No 1 Litchfield, NH 19,958 (22) 78 No 1 Wolfeboro, NH 16,329 (18) 78 No 1 County of Coos, OR 27,215 (30) 78 No 4 Salem, VA 22,679 (25) 78 Yes Total 90 Total Existing Capacity 1,969,488 (2,171) Source: Information provided by Ron Myer, EPA Office of Air Quality Planning and Standards. 335 Table 1-3. Inventory of Large Municipal Incinerators in Operation in 1980 State Unit location Connecticut Ansonia, Stanford, New Canaan East Hartford, Bridgport District of Columbia SWR Center #1 Florida Orlando, Dade County Hawaii Honolulu (Waipaho) Illinois Chicago (N.W.) Indiana East Chicago Kentucky Louisville Louisiana Shreveport Maryland Baltimore, Baltimore Massachusetts Saugus, Fall River, Braintree, Framingham, E. Bridgewater Missouri St. Louis (S. First St) St. Louis (Grand St) New Jersey Red Bank New York Huntington, Oyster Bay, Tonawanda, Lackawanna, New York City (Betts), New York City (South Brooklyn), New York City (Green Point), Hempstead, Brooklyn (S.W.) Ohio Lakewood Pennsylvania Harrisburg, Philadelphia (E. Central), Philadelphia (N.W.), Shippensburg, Nashville, Weber County Tennessee Nashville Utah Weber County Virginia Newport News, Norfolk Navy Public Works, Portsmouth Wisconsin Sheboygan, Waukesha Source: Information provided by Ron Myer, EPA Office of Air Quality and Standards. 336 Table 1-4. Manufacturing Segment of the Incinerator Population National Industrial by Use Category Use Waste stream Units in nation Solid industrial process 620 Volume Wood 260 reduction Trash 620 TOTAL Volume reduction 1500 Toxicity reduction Solid industrial process 170 Liquid industrial process 420 Sludge 50 TOTAL Toxicity reduction 640 Copper wire 400 Electric motors 1000 Resource X-ray film 100 recovery 3 Steel drums 40 Brake shoes 40 Other 130 TOTAL Resource recovery 1700 b TOTAL POPULATION 3800 a Population figures given are maximums of expected range. b This figure does not equal the sum of its components because it is rounded to 2 significant figures. Source: USEPA 19 80d. 337 Table 1-5. Hazardous Waste Incinerator Vendor Data for the United States r* e a c «n o 3 w • §: e • * ii J: ++ • I 2. *«l C ^1 £ I 91 9 4* 4J Ml M 'V't* ^ | Ml M «l © 1 3 2 •• *8 H • ■ • *9 ■O s ► 4# • 0 • *■« * ft* T> 9 • • ~4 « • • 9 • *0 w *0 mam > _ * tft 4* U C C II U W > • 82 <4 J. V S T X w ter 6 *^0^ ■ CL fH TP CL ■ O TJ * 0 9 0^ O' O H ft I — oo O T3 • t a *4 a J j M 3 1 T» u ■ c •-« I: . •**%»* IO • 9 V- _ O TJ Owe ■ ■ ■ «H L- I* < • W «o H s 9 M u O » O O M M •J « / * 3 M 8 *4 W 3 1 3 338 m l . «. K P La 8 •4 u Pa •] 1 § 8 * 9 «M •a e •a 0 H | p J 8 —4 «a £ S • s 5 9 U ■ 1 -a 26 c £ S c 40 • p i mi • 9 • aa ci s S £ • 8 if 9 9 mmi mm •a p 9 s — • hi m W 40 m I ■ • «* 4i 9 8 : i ISf a - s Jf*| M 0 M la a-a J © C X fl «< 2 *J 8 &*“ 44 m C w 3 ii! 9 «-» •4 • 9 : 2 1 : k a. ^ a* ■ C 8 K 9 9 • 9 X ! si C «aa • • j mi 40 82 P* • ft- - » 8 5 8 * H • H lis f 11 4 1 la a 5 i u 5 9 an Ill mi A* «* 5 E ■I £ ■c %P • 8 S < 2 • a 9 Q m« mi 9 ^3 c mm 9 5 < fc- ■ • O mi m rni • 44 9 9a 9 9 p 4a 9 9 9 9 9 Q SOS 9a i 4a 44 • •* C 9 1 E 8 ~ 8 8 < < 9 9*94 S J f t ml ii* ■ UK 168 s Pa P4 «a | 0 . £ 0 M 9 9 9 la C — Ks9C < 9a •: • i 9 *9 • 4 a k 9 la «a 3 8 99 9 a 9 •9 mi O 4 mm 9 e s 25 •a •a 8 1 1 III •a 0 w wj 9 m» m m 9 1 1 8 1 u cr 1 «i • 9 u c 9 & e 9 1 mi 1 9 9 X 9 8 3, « ^9 •a 9 mi • la ►s . 44 9 •* 91 H 11 X p- W 4a M c 8 1 - sun m a er 0 9 a-« 1* Si 8 t •a •a Gt < t hi «* .1 51 *:l i I i • 1 1 1 1 0 7 a 1 ! a 9 g£ — a 1 41 »A 10 8 . aa m mm la «a4 s- ? 2 p- uK X < H « s aaa 4 ^ * $ • • a»s m 44 2 O • • t» y • e ~l K • • •si X M C e 1 e 7 ! 0 O 4 a "S 9 9 94 ♦ 7 I wa -j f **“ 91 9 5 44 j • s • y 8 a 8 i 4 j • 8 pa 44 a 4* a 8 4a •* E a t a <3 a 9 • •4 44 9 a n 44 W 8 la • 9 9 4 9 9 C mi • Is mi mi 3 • & U •a • l! fl 9 !i I 9 5 4J 1 &Z 0 la 9 8 P« 4 M *0 ?! O U 44 1 mi 40 9 Is • -• c 44 91 1 1 mi m £ 1 la Oft K £ c 8 •a pa h» i s N N •9 4*1 H N 91 N <9 94 rm 94 94 X 8 339 Table 1-5.(continued) ft* o 6 d i a| ,li fl • u 0X4* a . . . 8 • 2 1 4rt • ft* Ad O V Ad • • 0 ft* 44 Ad 0 44 Ad a* Ad fl u a a e art 4J ! I- 0 * o e Ad • ► 4 3 Ad 1 ; • 44 4-d Ad art a • -* 1 flee art fl Ad 44 0 !*? 1 art i ft* a art fl «Ad fl O A* M X r 4 * art C3 i! i Ad : *• ■ST Ad 0 A4 art • m a Us SB ■ 0 44 111 X fl Art Ad Art * Art fl D fl. Ad Jft a* ana 1 Sc • 4 1 I li' 44 «H a •J J 1 •» • Ad 1 «A« %4 °l £ S I 5 S 1 1 • ^ 3-3 _W (■> 1 H l. • • Ad * a ■ s • • Ad 5 c 1 Ad M • • | x 3 ,5 •H 4a ■ H | « b h 3 > 3! H ni w a h i s • K a ni t* • M aw a ^ M | ij ^ o • Ad • 4* flft Art Ad 1 2 ^rt rt 2 5 2 4a Ed 1 Ad 4* / 1,55 2 3 HU * c S' 5 X-,' 3 8 Ca. fll g •5 s 2 . B 4* fl Ad ft* H| V ■* 2 3, TC «|i:}l ^ did f 1 • rt O fl N O fl Ul *4 Art ft* £ * 2 2 2, a a a t ►b Ad 4# Art i * *a iiis **© <#——• — Tii* u * * 5£s88 1 a 1 8 N a M a J, ■ w ■ vvfe! •AON n^|i o ni r> a 1 1 § « e Ad S 8 ^4 • <3 r 1 • • to li- 9 .5 . . u u m m a Ad * e 1 O « 5 J*" 3 See 3 S e •• K !! o w o o O Vi ft* 0 4* 1 a a a a. 8 8 art & J X A ft* *3 Prt • • £ &2 Ad « ft* 44 « x "2 Ad fl xi M 44 a •J i. 1 • 44 J X Ad 2 i! A 4 t a M •i rt • ll t •. a 44 a ■J /I •I a fll fl! w m Ad a4 • •ft | S C "i 1 i 4* Ad • 4d Ad ft* a 8 • A* 11 bI a J a 8 C a 4 3 3? ■a* • slJ! 1 8 : 325 a • • Ad 3 $ 4 I li X fert • ft* l A* 4a o t & 1 • ft* t • C ft* A- O •0 Ad 11 a t 3 • id 4* 8 t 44 J B 1 H j! i © = r* ** •rt •ft V* 6fl • 340 barco* fyateaa, Ik. Haad Hearth 2} 600 pph Insecticide* Alao developing a rotary possibly other* 260 tpd Munic. vaatea plus hearth design liquid H.V. X) I c c 8 • LT) I H t tf 44 T3 O 9 •0 0 aH 9 • 44 9 Y* ^ < H 8 3 8 1 d 44 44 9 9 4 . — -4 44 9 44 • «*H - i *3 3 is 2 a k M M i t 8. • Ai s H vl 9 U 4> m 4 la ip 5 ? ^4 is 4 1 I 9 5. 8» O H *4 $ 44 1 mm i; rH nr* 4i 9 8 a. 9“ 3? 0 ►* j 3 AM gm It u 8 i: 44 ilu H s: ►> •M i.e W at *S 6° nr* ^ “ iE w t) u *4 9 4i C 9 *4 5 V4 ■ 3 l 3 E2 31 ST 03 S in 9 9% 33 Is *« 3 C 0^5 D 9 U •-4 9 91 44 9 9 • 0 am ^m 9 9 m M • w w 44 41 8 g ► « J 0 •H to • 9 9 9 s •O 9 a-4 0 44 «H O • ~* 8 83 •3 : c ll H • 8° ► • «© a-H 9 1 11 • h i 3 8 .* 1 1 •H 8 M «S I *4 Q 4a U 0 9 9 44 1 © • u U %4 So V r .* 9 0 44 9 C • H C U si is 9 «O ||S E 44 «4 9 fl *4 C 9 or 9i • O £ m 9 ^ 9a U i-4 n 9 0 ! II I* !« © © o o H H a 9 1 1 ji If 1 l I ’ I •■4 n %,% i 3 M M 9* r* «4 9* m S . 8 & N i* p s §1 «k «k 6 «e-a »*4 M M 9» ^ H N H H 1 JS *4 n m 19 N 9 «9 S 1 1 n ^ 1 la 9 _ 0 44 o mO Jm 1 44 44 4- 4- 1 •• fl /N/N 2 g.~ « 1 1 “is! ? s i 1 a o • M M • fc S> 41 0 £ ::. • • 44 o . •o M © M M • • X aJ e> o ES N 9* •-I o m n 8 V 0 9 44 • • KH M9 ♦1 3 • • 0n £ 9 *• « — 9 O $ 9 i ** ^4H N b., -a oo am 0 W V*4 9 H CL 1 ^4 W O 44 I s Li • •-t 9 c 9 i o 0 ^a4 • 6 4> • 9 M ia Ji *9 la 5-0 0 W nm • «v4 #» _ < * • XI aa •• o o • 3 « e q e & »■ F^ « o L. 4 ■ t!*! l< aa *n 44 £i 4i a - - 9 6 a 4 nri 4- aa M 9 ill 9 ** • at £ - H • aJ 2 3 9 9 *2 Pa • • M ® a! as 5 b w w II*? £ JB "8 £ *3 3 a k • -6 T- H b ^4 m*4 9a 9 *1 2 u r K 0 a. • o • M • •a « M • M a o SI 9 * • m • a. j] *9 • C 5*. | 6 as o 4 s? 8 • o H ? • *4 44 fr 8 M 0 nr* 44 9 0 O 9 %* m s 5 M *4 4a S 9 o M w £ • 9 44 9 oa 44 9 0 44 t } • 5 6 frS 0 M • *4 8 a £! 3 1 ■g 9 a-4 I J ! 4d < w 9 %« 9 J a f i * f 44 H i 1 44 II H £ • 44 £ £ K Si la 4a 0 9a i N r» r> r> 3 *n n 9> f> a R O -9 341 Fllbrlco Co. F.B. Unk Custom-engineered «ita; not actively marketing Table 1-5. (continued) 342 Table 1-5. (continued) mu 3 2 l • 1 *3 J • H B ]ij J tu w2 fc* I f t c r *« ? • f i. NK « j a ib -h m K o ? • • • &g g£ 3 N 7 >< • -i 6 • •*u a M M 9 C -« d o •H CO to to E w d ctJ 3 CO TJ 0) 01 3 lA X o IA c o u i! a; L. O c o c > 5> o c in «TJ I a; ♦-> vr> n? * CJ JZ CJ C 4-* c o if § « w- -C u ^ *-J 41 (A Oku k- C O' O «J TJ ^ -C 3 u: ZJ -h CJ V V) * 6 t k. T3 •*-» o c t H D w £ U • - M (/) O' u C C «-» O ■Q JZ H) 3 U C •H VI 4< k. W c o C 4IH 4 M £ > O o 5 V " *5' TJ 4* * T) k-J Ci C « C « C 4» S'J* ' »~4 4-J r-« 1 5 & 5 u -g 4 ^ O JZ c u « (X u k- 4J C <0 5 8 i u rg o > 3 i/J e o _ c 4J •—i >* oj5 4> 4-J 4-» k- .c H k- O 4J O c u. k- c m m i x: o —« k-l U • k. W) - § i 4-1 4J '*"• ♦-* • 2 J 8 O i t o r. £ k. *J 4J V) 4-J 4) 4 t5 O to TJ - § 4 C o 4J 5 C M O Cl k-» JZ CJ o CJ I U 4 >. I • u CJ c * * CJ *H H O S?5 u • H l/l « . 4-J 4 c -» 4J >.k > k-» -H 3 O XJ U) i C TJ 4; - i k-» k. <0 4J 9 * r r~* f—i 4 •0 >t 55 ! 8 *.! w C I C C | t Ci I a n i W) c < i i j JZ o» c ■n a o 10 <0 C C B o o o J 15$ 3 to 3 IO £ H CJ « L ‘ 5 5 H ^ ** 5 U i « £ C • O 10 •h c w o <0 k. (/) 2S.5 o »0 JZ O' O' C C O' H »-» c H H a. a-H o o a. u k. ♦J *-/ V-< u u o 4J Cl XT 8 § 8? u u x> CJ if) U) JZ Cl C O' o TJ H ■ 3^0 *-< 3 u U» rH «k4 O M 4) D. O' > c 4J k-i C ♦-» VI t c <« tX i co a. vO r- cd O o o o o o H L> & 8 - 4J O' 2.5 CJ k-> a « O 4J u O' w c •H «J a cj 4/ x: u a 4 w *j -H 10 Cl i t I 8 Z 8 u >0 k. 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Ci o 4-J I-H (0 -C « u > « 4-J U4 C ° 8 3| 2 S U k^ Cl 4-* 5 3 i "Z 8 *0 k- ■ a o o 5-5 5 8 S k~ o TJ S CJ >4 -C CJ 8 I S U u ° l >k u ■5 CJ I o 85 | tj 25 5 5 8 8 u k- Ck «44 6 8 •o -o 3 I 3 W CJ «-J CJ C kJ c k-v « 41 k-J 31 C m a *i a vi « « * h 8 “ O o kC O 346 Candidate _ Incinerator type _ EPh hazardous for incineration Liquid Rotary Fluidized waste mgtoer _ Hazardous waste _ Good Potential Poor injection Itiln _ bed a fc* £8 it H fel O H u u x: -c u u c c o o a2 C u u 1! 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O X *J 43 W U ■3 41 43 fl rH U, W U W 4-1 C T3 W C rH 43 a W •O 4-> •H W * £ XJ 41 S 3 o If H X 41 O U U 43 *J E g 41 W 41 - c •S 5» £ § ag u k- C I- H 41 N Uu n O' m fH 359 3339 _ Ferrochroie silicon furnace eaission control dust or sludge _ 3339 Ferrochrcxae emissions control: furnace baghouse dust, and ESP 3339 Primary antiaony-pyrometallurgical blast furnace slag 3341 Secondary lead, scrubber sludge from S0 2 emission control, soft lead production 03 03 H s h T5 3 ° S5 &S! 4» ♦J • <0 k- ■O i C T> H C U « C U H v 1 _ 00 CO H c c TJ H 4) C U 4.4 * C o u CL U o U-4 •o 0 5 3 u n i: * w &; s u «i 4* 4-> « « > w 3 1 u i %) 5 S I g ’5 i 5 8 U 4» 5 C X k- a = 5 § $ 3 ' *-« i v> i * ! 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(continued) j! .S % S c « 0 •H O 4J C S 5 H C ♦J «l 3S Is C X i J! 5 8 O' O' O' s A O' O' s A o in r p' O' O' O' < •3 £ O' J O' O' O' O' O' O' H IN m ♦ O' O' s A § o OD O' S A O' K K S • • • O' « O' O' -M O' A U A S S* OD « O' &-3S ii A S lA -« O' *-< O' O' O' 4J 9> T3 & S' St '2 ii § tr -4 C VI -4 ae M f s o C 4J 01 0) 4J 3 & d 2 9 O • U <-4 o **-< I * -* -4 C *j x: « v m 9 «-> O « -H £ « 5 « fN i t) ^ C a>t) * >* o ™ • c c « *j c ^ ecrec.Ce -<43 c c m 2 o c r. ®-hc 5-4 * » 9 p >• 9 «Q Q jsO O >• 4 j H - W b N M M c r' d> (T' r a* ^ 5 -< £ *- -* hslls U 4 ^ u 0-4 r- f ,N r N < < g 2 S* 5 T3 U C 14 O -4 4 L 4 -4 S- 9 3!s I 364 Hexachlorocyclo- Liquid injection 2450-2512 1340-1378 0.17-0.10 MR Total organics pentadiene 94-99.95 Waste constitu¬ ents >99.999 Table 1-9. (continued) U ■§ X u > z Is u u u H 01 TJ «M j St .2 & 4J C It § & ■H C 4J i> I s O' a. o 8 c u c •H 0 U 2 Rl & E S 0 >1 *- 4-1 D. 0 s 3 0 » 0 0 o & 8 0 u 8 0' 0 O' (riff 1 ■h • w • r. O' in 8 A 88 Is ■h • 0 • S O O' O rH O • A 3 A i e CD *r> ■D 0 I l IN fN — * 0 £2 0 T3 is 0 TJ C 3 8.3 c -i o u 0 d ? c w ^ * *0 ■ p -I 0 IN * c 0 u r- o. -i *n ■C 0 W £ 4J kl *J -*h + cr m x) c eat n c -1 — -H I r- xs 0 |?i 0 u £ d a a S O’ P? °# "3 IT s 91 * 18 w ai r.i U g IT 0 9 c * N ■a ■a & o 0 ^ -4 0 4J 0 >-iJ n u 5 * J J U O' &? 0 ® 3s; £ * D IN ft 0 ® 0 0 l*' O'® 6 D^f •O 0 I" .fl 0 ® • M • Ml * S ? t f a n r U 0 CD fl 5 i 8 *j 365 Mustard (che»- Molten ®alt 1652-1832 900-1000 MR HR MR >99.999985 ical warfare combustion >99.999982 agent) Table 1-9. 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J >* o x o 0 *4 u 4 a >* *4 A >% -*4 N Q ' • 3 3 N 9 a >» 3 3 Q l A >% Q N -3 ^ d u i • q q - 3 Q * 9 a 3 N M 4 a I 5 3 £ -4 U >4 V A u q 3 • 3 u q o 3 3 3 ° N H S S' Si 43 U 44 4 • cj 3 H q 5 13 >% A 4 41 c o 5 q 44 2 I * 73 If 44 >% *-4 a si 44 44 a o w *J 53 >* q 3 9 H A u 01 9 43 a. q -4 3 £ 9 « S 3 O O W I 3 3 a a *■4 q o 44 9 3 1 3 —* 44 X 43 43 CL C /1 o 1 4 3 44 Y ? O u o 9 43 Os O 3 44 H 3 44 43 a. 0 ? d 1 t4 a q « 9 9 3 3 H H O O <0 3 a 1 5 3 3 w o TJ U >4 44 A ^ a >% t-4 a * -9 Q a a ^4 q q q a s -4 q r4 *■4 ^4 ^4 X -4 a a 3 3 3« >s a q 3 >s A >* a 0 u 3 3 5 3 3 >s a Os 1 04 1 44 q a 1 A 1 ® J 44 q 2* a 1 44 q 44 q 44 •4 O 1 a 1 a 1 a 1 a 1 q a a 1 on 3 *■* 04 on 3 CD* »“4 •a 3 3 3 A A Q. •H 04 04 os a ~4 os a q 04 a a O -9 04 04 04 ^4 a ^4 o u Os <44 I H a 3 1 q a 44 3 43 o d tJ q 43 *4 a 3 • 43 i ■3 O 44 a 3 3 I O 44 ** a a N J fid 44 A 4 9 u s H **4 >4 >» 43 43 44 44 ui ui 371 Hc/MW H c /W Hazardous CoosCltuenC kcaf/gram Hazardous Constituent kcal/gram G* in os ao vO 04 >o CM ro Gl 03 •*4 04 o* e-> 3N o O in O' « o* in G> *< >T o oo -4 <3> 33 o 04 o o >* o* >o o «n V 0 o -u r>* ao m in »n z 00 vO m m >o 04 >* r>* »40 o% r«* vO m vO m 04 o 4^ 04 o* cn -3 ^4 o a u >> X 2 u a u h 7 r-t — a 04 1 CO z a •3 a □ a c a **4 c cu u ■3 a G 4) G i 5 a a a 4-1 •*—' a xu G a a -a a u Q. G x a V G a a a a a O a a a 0 a a G ^4 D *■4 u u *■4 V a -c JZ M s 1 OJ • •3 a u >s 3 3 >4 G <3> G a c ■*4 •■u c CO JO a 3 3 JZ ^4 C G —4 a a *-4 a a a i • 44 0 a ^4 ^4 44 >4 >> x4 c u **u ■3 q 0 • e a JZ 4* u > >> V JG JG > O -3 ^4 •3 04 a c 0 o a a C • 3 3 >% jg JG •“4 4-» 44 •■4 *■4 u x4 x4 • Q. • N a u c c 3 V *5 3 z i JG i-i 4-1 >s a a >4 Q U 0 o O 04 c a u c >-U **u z u 1-1 a 4) JG ■ a «c 2 c a U u u a 4J ^4 .G a 0 0 0 O - i a a a • 1-1 i T u Q. u o. u u 0 JZ a c Q. a u C G y •*u «H Z a z z 3 0 0 >v a CL a o o o 0 ^4 u 1 ) 1 G -3 T3 -3 -3 1 a 1 i a a c =u CL a ^4 U T3 u u u u q *3 u o JG 3 9 -4 0 0 0 0 o o o o o Q 0 Q o Q >4 >s >s c 0 o o O *44 a >» cl 3" T a a a a a a a a a a a a 3 a 3 JZ CJ Z 0 4^ «4 e *3 <-u o O o <0 o o o 0 o o o o 0 0 o o 0 0 u *^4 a *44 2 X JS 4G a a CO u u u a u u u u u u u u u u u u u u a -3 T3 -C u u u O o *4 o 1-1 4J *-» o 1-1 44 u 4-1 1-1 4 4 i-i 4J 4J i-t i-i u u 4-1 a a --4 1-1 a a a a a 0 >N >S u *•4 u *H ■—4 •H ^4 ^4 x4 -H ^4 *«4 ■H a X a a 4-1 4-1 4U Lt c c C c 4-> z z z u z z z z z z Z Z z z z z z z u 5 u u c G G G a a a a i 1 1 1 1 1 I 1 1 1 1 1 1 1 1 1 y 1 a a a a a a -G -C z m z z z z z z z z Z z z z z z z o r^- Os cu flu Os Os cu CU Os flu a- « « « a a a a a a a a a a a a a a a a a o 00 m 4^ 04 >T sO O «n sO Ol p>* T in m o o o. o sO 3N n in in 3N in n 04 in in in ao m r>» in m a* <* "** 00 vO vO » a a JG a q J3 a a a y o •X •3 a G *3 u 3 *H U ■3 G G a O JG a O 3 0 Oft JG 1 lx Q. o y o O a 0 a 3 >-4 o. a o u u -3 a v w a o J 44 >s *3 T s 44 JZ a X G q <3 a >-4 a c JG O 1 a 1 a s 1 a a c 3 a 44 0 «44 44 t a u 3 a 1 Z a a a o u a >S xU O 0 0 44 a 3 5 43 44 a 44 3 JC >4 u 3 O *H *3 ■0 *3 44 1 2 a N >* 5 44 C 44 G a 3 a a J= a u Lt N a u 4J a a 6 a a q c o u o a G Si *H c a y a a a 44 1 a a a 3 a 44 a 44 o u 3 G 4^4 0 G a U O a 4-4 5 a xU a u 44 u J i W U i a J3 44 u 3 a a 0* i a 3 ■ a 04 1 1 a 0 a 3 a 3 “3 u O *H H M X *3 a 44 44 04 o z a O a G H a a a a >4 4-1 c n •H a U z 44 a a 1 r-4 T u at a 44 >s >% >4 0 N JZ a 4J U u 4U 4U 44 a «C •-U ■ fl XU >s H a z fU X X JG JG a a G 6 c G H u a >4 >4 >s >» 31 >s >s J3 >» CL 44 TJ J Q. 44 44 44 a o a a a u 0 J u G & | X JZ -G X H J= H -G 44 X xU u a J3 JZ jC u -O 30 00 G 5 i J 9 i UJ 44 1 >* >s 44 >* >» 44 a 44 >4 >> a 44 z CL CL CL 44 u o o 0 a O o. is J! ii • JZ -G a J3 -c 3*3 31 JZ jG 44 JZ i a a a 0 u u u u ^u **H u u 4-1 44 4-1 X 44 U X 44 44 X 44 44 a CL 'T 7 z z y Z 44 44 44 J a a a a £ ii 1 1 * a a 1 31 a 1 l a a 2 a i l x4 •U z X X X X X X 04 r X X Ol X X 04 X X X z 04 H z CL z Z z 372 H c /W lie /MW Hazardous Constituent kcal/gram Hazardous Constituent keal/gram «««« « «««« m « « m « « « « r"»^-4AiA«-4A>y-*yr' , >CMOc"tO^»d*>r>y.^®30^a^'^O*A (NO<^^iAi/>a)HN<09iAH<^^^rsaOH3}a)aoao®0«T • ••••••••••.•••••• •••••• a • CM-rOA^OACMO» c 0 0 o a i a *H 44 44 cn 0 U 0 jd 0 0 A o 0 a 0 0 0 0 A ^4 o C 2. 3 0 44 0 c c 0 O o 0 0 u 3 a a a U H ^4 JS 0 u c 0 d 0 z a o o 0 *0 O 0 a 44 44 w 44 0 jd -c • u H C u X 0 0 0 3 Q. a. 0 CL A •0 5 *v4 0 •o 0 0 0 o 0 0 d p4 0 o d o U 0 M 3 X 0 C u u u C a •44 u u 0 u 43 0 0 0 44 0 0 A 0 2 44 0 o o 0 o 0 o a. 0 U *d U 44 0 a *0 ■A A u 3 0 •4 3 H A 2 A 44 44 0 d Q 3 H js o u 3 0 0 44 ^4 U 0 H o 0 0 *■4 3 ■o 0 0 0 3 0 0 0 0 0 a 0 9 « o H X w» 0 0 -a 0 0 ^4 ▼4 0 0 0 o ■ « « r* CM sO ■0 a d © sO 15 at. < z 44 Us « « 41 « « « 0 « « a\ CM 9 CJ CM r«. ao ao (A m © o> o\ ao ao ^4 CA CM r^» so kA CM >y ao s-4 sO O A ao sO 'T • • 3 O m ao 00 -T »o cn sO 'O SO ao A CM CM . <3* O' in ON o in 1 d 9 0 a ^4 u *3 d >N 4 o d Q. ^4 9 a. a. C M o X o o M a Q *d X d d X d d d d O o 44 o 0 cd d 4J u 4 d d d U *4 2 d 44 o 3 d u d d u u ao d 0 O i X a u d Ps d <—4 d a. >N Oa o 4 '•44 o o 00 Ph 3 a H H a. >i 2 u d u d >N o d u u o H Oa ^4 ^4 M 0 0 X X 0 o d d H *4 9 2 d o u o Q. s4 d u u o o 1 0 *4 q 1 d 0 d d U U o —4 u U 4-1 O M X H H X X -4 2 NO u d m a u O d X a 0 H u Ps h H H o (J 1 1 a > r 4J o *■4 • • 9 d d d • *4 d 0 • 4 *4 • d X U m ^4 •H #i •H H ^4 a. a* X X * CM a x H *4 aa a 4 a x cu H H a a CM CM CM •H H CO AA H 3 CO > AA >-> e S-^cS •H TO OC 1 *-* 3 <1) o w a 3. 4-> cw <3 3 O 3 S EC 00 O 3 U «w •H lw o AS 3 to 'cn 3 iJ *rl K 3 ® •H 3 •u a: 3 4-1 3 O 3 On! Ah U O 3 i—! AA 3 H I = <3 2 O *4 u T o m o in O *4 CM ON ah CM ON ON «n X CM O o ON B oo <—* CM CM >T *n in r-* rs ao ao -4 ^4 CM o 3 d X *n o o o o o o O o O o O o o *-4 *n *■4 •n ^4 ^4 H •n H ^4 ^4 -4 Ps X 0 3 9 /-4 9 o u A >N X 44 d >1 X 0 2 0 d 44 0 o d d d d fl CJ d H— 0 d AS 4 3 *4 •4 2 44 d 9 d W d N CJ d o 0 2 73 9 44 • o d u 44 d u 44 0 a q «n 1 g 4 d o 0 d 2 J *4 44 - 2 u x 1 d g ^4 u Q 0 0 44 n u Q o a k4 U u X s O 4 A o X • t d w A 0 r - 0 1 a 4 J 0 0 ^ a O M J h O H 1 O U o 2 U 44 •4 d o 2 s 2 CJ o o 2 2 ^4 d d 9 X M 0 H o 2 0 2 U S X 0 d CJ 2 44 9 0 2 O r* 1 CM H 1 CM o V4 X O 4 X o 4 X CJ 44 0 0 w 4 o O a4 4 o 2 X y u X3 3 d d CJ m 0 d CJ u d o u § X CJ d 9 « d ^4 CM a a d 2 U CJ s4 U H 4 u H CJ «n a 44 d H 44 d H 3 X X Q d d Oa i 2 X CJ 2 CJ d >N CJ ^4 U H 3 a 44 d H u d Ps a E o 0 u 0 1 ►4 44 9 H H ^4 ~4 i CM H i CM 4 44 d 0 Oa 4 aa 3 2 a h 0 3 X 374 Nitroao-N-Aethylurea T3 CU 3 •5 C O o CM M cd Ph O o o pH H CM CM CM CM CM % 1 o 2 T 0 U T3 4 >4 U 43 *H 0 0 CL 7 a *d CO z m H a Q • •*4 s —<• CM d 0 1 aj 14 "H •H ® U 0 H O V CL o cs 0 a o u 43 o a J 44 0 ^4 0 44 0 0 u 0 CO 44 o »-4 0 3 U U Q. X 44 0 a. N x 0) 2 44 3 0 a 0 fl p4 2 3 Y PH pH U O © e a O •H 23 o 44 >l 2 CJ >* pH ® , 5 44 0 -C ■H * 44 --H X fl CL 43 q 0 2 44 43 O >% 44 pH ^H 1 O U fl 5 a pH 0 44 3 * 0 0 • 1 • U M 1 m >\ >* 3 pH 0 /—4 2 S fl CM m l H x a Q H >% p4 o 3 3 1 pH 1 >i M 0 a 3 •H >4 >4 pH X >4 -a 4-1 3 • 6 0 -pH •H 1 fl Q a 43 0 43 0b > 2 u fl 44 G X 0 0 H ■o 44 CJ • ■H fl 0 pH a 1 44 • 3 32 0 44 o o a >N • O O pH 3 u >4 o 0 1 H O. 0 >s jC 5 0 u 44 u o fl X U • w o -3 u 43 u a n >s u 3 43 O. w u 1 H o 0 m pH 2 44 3 o q u T 44 44 43 0 fl 0 1 0 pH •H 2 u U 0 5 >s 2 fl 0 0 • H T3 CM 44 a 0 0 U CM O >s *H 0 44 u >« u i ^4 X •a u T f a O 1 0 a o u 0 1 H 44 c C Y «H •4 u * 0 X 44 Y CL o 0 pH a O O pH a • m 3 pH pH >» 9 0 3 5 C «4 u 5 44 * O >4 M u >1 o u w >s o pH -fl >> X 00 0 X CO •S3 * ° H X CJ u 43 O O jC u O O ■ 2 a. u >S *H * U pH >% 3 >4 43 1 44 «H 44 • 2 2 44 0 44 H 2 2 2 44 -H 43 44 2 1 0 44 0 it 9 3 44 ■H 44 0 • ■4T O a i * n 44 w 1 44 s • T g J u 1 u "H Q Q 3 z 1 V o 1 44 pH z 1 0 H 44 ^3 >-p 1 X w 1 0 1 Z 1 X CQ CM >—• u m i ~» Q a a. Q Q a z pH CM X X z Q Oa H CM CM CL u 376 Heat ot Ileal of Combustloa Combustion Hazardous Constituent kcal/gram Hazardous Constituent keal/grau i-prpp*y'Or>«sr«pr*(*’»OcMXaO0N<" , >‘/ , 'OOpH<*>< , O>Or'upp»pHCM<" , »mcnp**c , 4 3 0^ —4CM .*ncnyu"isO'O^O*Or'*r^r*.a3aO®cDaoa0O'O'ON fl 4 u pH X 0 2 X 5 u ■fl •fl pH 0 0 X 44 X fl u 0 0 1H X X X UP ■fl Jd fl u X 4 pH u 1 pH ■fl pH a •sH 0 X X X O 0 0 ■fl CJ Os 0 0 *fl X 0 CM O X £ p fl fl pH -H u fl ^4 fl 4 H a 2 A H pH 0 . 1 1 U X «p4 pH 'H X X 0 —H pH 0 X CJ 4 fl u pH u pH pH 0 U4 0 0 *fl X 3 X X fl fl u pH 0 X 4 pH pH u X 0 U X fl 1 X pH 3 -fl O 0 Os u u 2 4 41 pH fl u •fl U 0 u 3 44 0 . 0 fl X O 0 pH pH fl 0 0 0 0 0 pH H kP pH 0 O 0 a a 0 u X u u O 0 fl 4 0 w fl S 3 3 0 X fl X fl 0 CJ X a fl e 0 a X «u« u pH ^H fl pH 0 . pH 0 u 4H O a. X pH pH pH c 4 H 1 1 0 •H 0 a 4 ■fl 0 fl 0 pH O X 1 3 pH O Q 4H 0 •H 2 CJ X X 2 0 fl X e • 44 a X u 4 0 X U 4 u X C fl fl X 1 1 £ X X X 4 fl 0 X 1 . r>. 0 4 0 h - • 3 1 x u A A *-» a. X a. pH x 2 0 a x A X A 4i 0 fl o 0 O u z I z I M 0 0 5 3 -H u a <4 o u o H X u I a 4 u 3 O 4 ■fl 4 u 4 pH i 0 0 O 4l 4 O 3 3 .. - U fl J3 A ■pH 4J 0 pH *H O pH H3 X X U X pH X m o a. 4 fl 4 o u 0 0 u 4 3 3 4 a 5 i I 4 a 2 3 -4 X o u u u U S. 2 4 O. u pH Q 0 *H 4 0 >* ° X U pH CJ 3 * ? u ph T 0 X pH 3 -5 fl O cj o u ■o X -fl 0 3 fl a a ci 0 x 0 0 3 3 2 3 O 3 U —t 0 5 3 V cj o x o V 3 CM U 0 3 u *0 X X a 1 <0 0 3 a. -* u x 0 X 4 *n 3 2 4 0 30 0 o pH fl X 4 X X u O fid 0 3 9 *->05 3 9 3 •fl X X O O* ti 4 O ^4 O U X 0 fl 0 N 0 3 4 a h 0 Os 0 fl x o 4 4 O 3 3 3 o e v a 3 ! 3 a u A 3 A CJ flu I I ci Z 0 a o s * 1 X U X X u o. 0 4 3 T Q y 1 X^-s S3 0 U X 4 —« up X u fl 4 O 3 4J N-' 0 3 2 I -4 3 3 O. pH -fl 4 fl w 4 1 m 0 3 0 I 3 a 2 U pH 0 fl U 2 3 O. O 0 o u z I z 377 Heat of Heat of Combustion Combustion Hazardous Constituent kcal/gram Hazardous Constituent kcal/gram ON on 00 in m wO r-» r-i «n ON o f*N m n* ao OJ i— C t/1 Q. O 3 -r- CJ *4- 4-> CU «— C t- 3 o cr> i/i .*>(/» t/i •>— 3 E . o 5) CM 3 c o •r- C 4->-- c o dJ d OJ JO E C/1 CO u (UU OJ v/i JO 3 OJ JO <4- r— 3 Ql CO. d d -r- CJ +-> LO cn r— j: 3 L s: oj CM 4-> tO • *»'4- • JZ fT3 O CJ ' 4-> CO CO d CU JO E • J 1 co d —. .C QJ QJ O JO 1/1 JO 3 QJ 3 <4- d QJ CO. CJ d •*— 1/1 +J Olt— QJ -JC 3 d 21 O CM V4- tn •» q) • jC JO O d> —' -*-> cO CO TO c 3 o 3. o <_> tn I— CO tn ao co z CO CM CM O *d- o CM to CO *0" I— *3" CO • • i— r-» JO CO CO u CO VO CM CO CO tn I— o «a- co VO QJ C QJ d >1 a. cO c !M C QJ CO ai c CU d >i Cl CU CU - c o aj im s- c >, QJ Q. CO CU c QJ c o d o o aj c QJ d QJ CO. JZ cr. o M c CU CO aj c QJ C CO d o 3 OJ c QJ cO c QJ O UO CO cO o 2 QJ 1/1 a j= d Vd c/i <4- O >i c (O TO QJ 4-> CJ QJ 4-> QJ •a o c a> d aj 5 at c £ JC co c CO XJ C CO QJ C QJ CJ cO d C i/I cO d O *• 4-> CU CO C d QJ QJ r— C >1--- d U QJ C a_ -i- TO aj 4-> u aj +j QJ CO □ 380 Benzene soluble organics (BSO) is reported as mg BSO/kg refuse charged. Table 1-14. Polycyclic Aromatic Hydrocarbon (PAH) Levels in Air Emissions, Solid Waste Residues, and Scrubber Water Discharge from a Municipal Solid Waste Incinerator 3 Compound Stack Gases & Particulates yg/kg refuse Solid Waste Residue yg/kg refuse Scrubber Water Discharge yg/kg refuse FI uoranthene 2.5 12.4 0.14 Pyrene 6.8 10.5 0.12 Benzo(a)anthracene + chrysene 3.1 36.6 0.15 Benzo(b) fl uoranthene + benzo(k)fluoranthene + benzo( j )fl uoranthene 1.4 62.5 0.032 Benzo(a)pyrene + benzo(e)pyrene 0.09 31.5 0.032 Perylene 0.77 17.5 0.030 Benzo(ghi)perylene 1.8 10.0 0.007 Indeno(l,2,3-cd)pyrene 0.77 <2.1 <0.002 Coronene 0.2 <4.3 <0.002 / a Incinerator rated at 2.5 kg/s, continuous feed, utilizing a wet scrubber followed by an electrostatic precipitator for particulate control. Other characteri sties: rocking bar-type grate with burning rate 0.101 kg/s-rr.2; primary air = 15-20% excess of theoretical, secondary air = 0-70% excess; stack gases = 10.9 m3/s (dry) at 293 K, 1 atmosphere; residue = 0.7 kg/s at 23% average moisture content; scrubber water discharge = 0.58 liters/s (input water totalling approximately 0.28 yg/1 of the Indicated PAH compounds). Source: USEPA 19 80 c. APPENDIX J ft AUXILIARY INFORMATION ON DEEP-WELL INJECTION 383 Table 0-1. Compounds that have been Disposed of by Deep-well Injection Chemical Acetaldehyde Benzene Acetic acid Benzoic Acid Acetone Boron Acetylene Boron Chloride Acrolein Butane Adipic Adic Butanol Adiponitrile Butyl Disulfide Allyl Alcohol Butyl Mercaptan Aluminum Oxide Butyl Phenol Amides Butyric Acid Ammonia Cadmium Amnonium Chloride Cadmium Chloride Ammonium Chromate Calcium Chloride Ammonium Dichromate Calcium Hydroxide Ammonium Hydroxide Calcium Oxide ftrmonium Nitrate Caprolactum Ammonium Thiocyanante Carbon Disulfide /Vnyl Alcohol Chlorine Aniline Chloroform Arsenic Trioxide Chlorinated Hydrocarbons 385 Table J-l. (Continued) Chemical Chromic Acid Ethyl Mercaptan Copper Chloride Ethyl Phenol Cresol Ferric Chloride Cumene Ferrous Chloride Cumene Hydroperoxide Ferrous Sulfate Cyclohexane Formaldehyde Diazinon Formic Acid Diethylstilbestrol Glycerin Dinitrobenzene Gold Chloride Dinitrotoluene Hexamethy1enediamine Dioxane Hexanol Diphemyl Amine Hydrochloric Acid Epichlorohydrin Hydrogen Cyanide Ethane Hydrogen Peroxide Ethers Magnesium Oxide Ethyl Acetate Mercury Ethyl Disulfide Mercuric Chloride Ethylene Mercuric Diammonium Chloride Ethylene Glycol Mercuric Nitrate 386 Table J-l. (Continued) Chemical Mercuric Sulfate Propargyl Alcohol Methane Propylene Oxide Methyl Acetate Radium - 226 Methyl Cellulose Silica Methyl Ethyl Ketone Silicon Tetrachloride Methyl Mercaptan Silver Chloride Methyl Methacrylate Sodium Carbonate Nitric Acid Sodium Chromate Nitrobenzene Sodium Dichromate p-Nitrophenol Sodium Ferrocyanide Phenol Sodium Fluoride Phosphorous Oxychloride Sodium Formate Phosphorous Pentachloride Sodium Hypochlorite Phosphorous Trichloride Sodium Monoxide Polyvinyl Alcohol Sodium Nitrate Potassium Chromate Sodium Nitrite Potassium Dichromate Sodium Sulfate Potassium Sulfate Sodium Sulfite Propanol Stannic Oxide 387 Table J-l. (Continued) Chemical Sulfuric Acid Terephthalic Acid Thorium - 230 Toluene Diamine p-Toluic Acid Uranium Urea Valeric Acid Vanadium Pentoxide Vinyl Acetate Xylene Xylenol Zinc Oxide Source: Reeder et al. 1977a. Table J-2. Modified Theis Equation wk*$re: X a 2.25 K H t S 10* 1/2 4 T1 KH ^h w - h bo x SpGb ^ 2. 3 Q • Radius of endangering influence froia injection well (length) ’ : K ^ K ’ « Hydraulic conductivity of the injection zone (length/time) H ** Thickness of the injection zone (length) t *» Time of injection (time) S = Storage coefficient (dimensionless) Q * Injection rate (volume/time) hb o « Observed original hydrostatic head of injection zone (length) measured from the base of the lowest • r 1 , underground source of drinking water h w » Hydrostatic head of underground source of drinking water (length) measured from the base of the lowest underground source of drinking [ ' water SpG b = Specific gravity of fluid in the injection zone (dimensionless) 3.142 (dimensionless). 389 Source: USEPA 19 Rid. Table J-3. Information on the Survey Waste Injection Program (SWIP) USE : The SWIP model is applicable for modeling the transport of momentum, energy and contaminant mass in porous media due to deep well injection or other sources. DEVELOPED BY : INTERCOMP Resource Development and Engineering, Inc. and INTERA, Inc. DEVELOPED FOR : U.S. Geological Survey, Water Resources Division REFERENCE : INTERCOMP, Inc., 1976, A Model for Calculating Effects of Liquid Waste Disposal In Deep Saline Aquifer, Part I and II, U.S. Geological Survey, Water-Resources Investigations 76-61, June, 1976. INTERA, Inc., 1979, Revision of the Documentation for a Model for Calculating Effects of Liquid Waste Disposal In Deep Saline Aquifers, U.S. Geological Survey, Water-Resources Investigations 79-96, July 1979, 73 p. ASSUMPTIONS: • Fluid flow in the aquifer can be described by Darcy's law for flow through a porous medium. • Fluid density can be a function of pressure, temperature and contaminant concentration. Fluid viscosity can be a function of temperature and concentration. • The waste or contaminating fluid Is totally miscible with the In-place fluid. • Hydrodynamic dispersion Is described as a function of fluid velocity. • The energy equation can be described as "enthalpy In - enthalpy out * change In Internal energy of the system." This Is rigorous except for kinetic and potential energy which have been neglected. • Water table conditions in an unconfined aquifer can be approximated by no capillarity and no residual water saturation (specific retention). • Contaminant reaction can be described by a first order reaction - similar to radioactive decay. • Contaminant adsorption on rock surfaces can be described by linear adsorption isotherms. • Aquifer properties vary with position-porosity, permeabi11ty, thickness, depth, specific heat and adsorption distribution coefficient. • Boundary conditions allow natural water movement in the aquifer, vertical recharge in the uppermost layer; heat losses to the adjacent formations, and the location of injection, withdrawals and observation wells anywhere within the aquifer system. 390 Table J-3. (Continued) Source: APPROXIMATING METHOD : t Finite-difference SOLUTION TECHNIQUES: • Reduced bandwidth direct • L2S0R GEOMETRY : • 1-, 2-, or 3-dlmenslonal Cartesian § Cylindrical OPTIONS : e Steady or transient flow • Solute transport • Heat transport • Wellbore § Heterogeneous and/or anisotropic media • Confined and/or water-table conditions • Recharge and/or wells BOUNOARY CONDITIONS : • Specified value • Specified flux • Aquifer Influence function Mercer et al. 1981. 391 APPENDIX K USEFUL CONVERSION FACTORS 393 Table K-l. Useful Conversion Factors ton, short X 0.907 = metric ton (kkg) inch (in) X 2. 54 = centimeter (cm) centimeter X 0. 3937 = inch feet (ft) X 0. 3048 = meter (m) meter X 3.2808 = feet mile (mi) X 1. CO 9 = kilometer (km) kilometer X 0 621 = mile U. S. gallon (gal) X 0. 0038 = cubic meter (m ^ cubic meter X 264. 17 = U.S. gallon cubic feet (ft ^) X 0. 0283 = cubic meter cubic meter X 35.314 = cubic feet acre-foot (ac-ft) X 123.53 = cubic met cubic meter X 0. 0008 = acre-feet hectare X 10,000.0 = square meter square meter X 0. 0001 = hectare hectare X 2.471 = acre acre X 0.4047 = hectare Hydraulic Conductivity gpd/ft 2 X -5 4. 72 x 10 = cm/sec cm/sec X 3 21. 2 x 10 = gpd/ft 2 Darcy X 18.2 = gpd/ft 2 Darcy X -4 8. 58 x 10 = cm/sec 395 302/2 -IQ1 REPORT DOCUMENTATION i._ report no. 2 . PAGE EPA 560/5-85-003 3. Recipient's Accession No 4. Title and Subtitle Methods for Assessing Exposure to Chemical Substances - Volume 3: Methods for Assessing Exposure from Disposal of Chemical Substances 5. Report Date 7/85 6. 7 . Author(s) Leslie Coleman Adkins, Stephen H. Nacht, John J. Doria, Michael T. Christopher 8. Performing Organization Rept. No. 9. Performing Organization Name and Address Versar Inc. 6850 Versar Center Springfield, Virginia 22151 10. Project/Task/Work Unit No. Task 11 11. Contract(C) or Grant(G) No. (o EPA 68-01-6271 (G) 12. Sponsoring Organization Name and Address United States Environmental Protection Agency Office of Toxic Substances Exposure Evaluation Division Washinqton, D.C. 20460 13. Type of Report & Period Covered Final Report 14. 15. Supplementary Notes EPA Project Officer was Michael A. Callahan EPA Task Manager was Stephen H. Nacht 16. Abstract (Limit: 200 words) This report, which is part of a series of volumes on exposure assessment, presents methods for estimating environmental releases of chemical substances from disposal sites. These release estimates must be used in conjunction with procedures given in Volume 2 (ambient exposure category) and Volume 5 (drinking water exposure category) in order to complete the exposure assessment. A five-stage methodological framework outlines the major steps that must be taken in order to estimate releases from disposal by landfilling, land treatment, surface impoundment, municipal wastewater treatment, incineration, and deep-well injection. The methods are applicable to chemical substances in all of the following waste categories: municipal solid waste, industrial solid waste (hazardous and nonhazardous), municipal wastewater, wastewater treatment sludges, and incinerator residues. The report provides guidance on information resources useful in completing each step and also discusses data gaps and limitations in predictive capability. Sample data and summaries of information resources are included in appendices. 17. Document Analysis a. Descriptors b. Identifiers/OpenEnded Terms Exposure Assessment/Disposal Toxic Substances/Waste Treatment c. COSATI Field/Group 18, Availability Statement Distribution Unlimited 19. Security Class (This Report) Unclassified 20, .Security Class {This Page) Unci assi f led 21. No. of Pages 412 22. Price (See ANSI-239.18) See Instructions on Reverse OPTIONAL FORM 272 (4-77) (Formerly NTIS—35) Department of Commerce UNIVERSITY OF ILLINOIS-URBANA 1 3 0112 112947863