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USATHAMA U.S. Army Toxic and Hazardous Materials Agency

ASSESSMENT OF APPLICABLE OR RELEVANT AND APPROPRIATE REQUIREMENTS (ARARS) FOR ALABAMA ARMY AMMUNITION PLANT, ALABAMA

FINAL REPORT

CHEMICAL HAZARD EVALUATION PROGRAM HEALTH AND SAFETY RESEARCH DIVISION OAK RIDGE NATIONAL LABORATORY OAK RIDGE, TN 37831-6050

May 24,1990

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U.S. ARMY TOXIC AND HAZARDOUS MATERIALS AGENCY INSTALLATION RESTORATION DIVISION ABERDEEN PROVING GROUND, MD 21010-5401

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DRAFT REPORT

May 24, 1990

CHEMICAL HAZARD EVALUATION PROGRAM INFORMATION RESEARCH AND ANALYSIS SECTION

HEALTH AND SAFETY RESEARCH DIVISION

ARAR TASK GROUP

Elizabeth L. Etnier Patricia S. Hovatter Raymond Struder* W.P. Teichert* Rose S. Weaver Robert H. Ross

*Lee Wan and Associates, Oak Ridge, Tennessee

Distribution unlimited approved for public release.

SUPPORTED BY U.S. ARMY TOXIC AND

HAZARDOUS MATERIALS AGENCY Aberdeen Proving Ground, Maryland 21010-5401

Contracting Officer's Representative Edward L. Newell, Jr. Environmental Branch, Technology Division U.S. ARMY TOXIC AND

HAZARDOUS MATERIALS AGENCY Aberdeen Proving Ground, Maryland

TABLE OF CONTENTS

Page

1. INTRODUCTION 1

2. SELECTION OF ARARs 2

2.1 CHEMICAL-SPECIFIC ARARs 2

2.1.1 Indicator Chemicals 3

2.1.2 Federal and state ARARs 6

2.1.3 Other Guidance to be Considered 6

2.1.4 Conclusions 7

2.2 LOCATION-SPECIFIC ARARs 9

2.2.1 Caves, salt-dome formations, salt-bed formations, and underground mines 9

2.2.2 Faults 9

2.2.3 Wilderness areas, wildlife refuges, and scenic rivers 9

2.2.4 Wetlands and floodplains 12

2.2.5 Historic sites and archaeological findings 12

2.2.6 Rare, threatened or endangered species 13

2.3 ACTION-SPECIFIC ARARs 14

2.3.1 Preliminary decontamination activities 15

2.3.2 Off-site alternatives 18

2.3.3 On-site landfill/groundwater treatment alternative ... 35

2.3.4 On-site incineration/groundwater treatment alternative . 44

2.3.5 Capping alternative 50

2.3.6 No action 51

REFERENCES 54

Appendix, Indicator Chemical Worksheets A-l

i

LIST OF TABLES

Page Table 1. Indicator Chemicals Selected for Alabama

Army Ammunition Plant 5

Table 2. To be Considered Guidance for Cleanup of Contaminated Soils at Alabama Army Ammunition Plant 8

Table 3. Selected Location-specific Applicable or Relevant and Appropriate Requirements for Alabama Army Ammunition Plant 10

Table 4. Action-specific potential ARARs for Alabama Army Ammunition Plant. Alternative 1: Off-site alternatives 19

Table 5. Action-specific potential ARARs for Alabama Army Ammunition Plant. Alternative 2: On-site landfill/groundwater treatment 36

Table 6. Action-specific potential ARARs for Alabama Army Ammunition Plant. Alternative 3: On-site incinerator/groundwater treatment 46

Table 7. Action-specific potential ARARs for Alabama Army Ammunition Plant. Alternative 4: Capping 52

ii


1. INTRODUCTION

The Comprehensive Environmental Response, Compensation and Liability Act of 1980 (CERCLA, Public Law 96-510) provided for "liability, compensation, cleanup, and emergency response for hazardous substances released into the environment and the cleanup of inactive waste disposal sites." The Superfund Amendments and Reauthorization Act (SARA, Public Law 99-499) provided extensive amendments to that act.

In particular, Title I, § 121 of SARA specifies that for any hazardous substance, pollutant, or contaminant that remains on-site, the level or standard of control that must be met shall be at least that of any legally applicable or relevant and appropriate regulation (ARAR), standard, criteria, or limitation under any federal environmental law or any more stringent standard promulgated under state environmental or facility siting law.

The U.S. Army Toxic and Hazardous Materials Agency (USATHAMA) has asked the support of the Chemical Effects Information Task Group in the Chemical Hazard Evaluation Program at Oak Ridge National Laboratory (ORNL) for assistance in determining ARARs for Alabama Army Ammunition Plant (AAAP), currently listed on the National Priorities List (NPL) (52 FR 27620, July 22, 1987). Supporting documentation for this report includes the Alabama Army Ammunition Plant Installation Assessment (USATHAMA 1978); the final remedial investigation (RI) (ESE 1986) ; the final feasibility study (FS)(ESE 1987); and the remedial action reports by Weston (1987, 1988).

AAAP is located in northeastern Alabama, 40 miles southeast of Birmingham and 4 miles north of Childersburg. Operations conducted during the 1940s included manufacture of the munitions compounds trinitrotoluene (TNT), nitrocellulose (NC), dinitrotoluene (DNT), and tetryl. Also manufactured at AAAP were sulfuric acid, aniline, N.N-dimethylaniline, and diphenylamine. AAAP was originally divided into three areas: the Leaseback Area, the GSA Area, and the Industrial Area. For the purpose of the RI/FS work, the installation was redefined as consisting of Areas A and B (ESE 1986). Area A has been designated for release and sale to private individuals; Area B consists primarily of the original Industrial Area and currently has limited access to hunters and loggers (ESE 1987).

As a result of the past activities at AAAP, the soils and sediments on the installation are contaminated with munitions compounds, degradation products of the munitions, and heavy metals. The primary site of concern in Area A is the Old Burning Ground (Study Area 12). However, the contaminated soils in Area A have been excavated and transported to Area B where they are currently stored in slab and awaiting incineration. Therefore, the primary area of concern addressed in this document will be

Area B. The primary sites of concern in Area B are the Sanitary Landfill and Lead Facility (Study Area 3), the Northern and Southern TNT Manufac- turing Areas (Study Areas 6 and 7), the Tetryl Manufacturing Area (Study Area 10), the Flashing Ground (Study Area 16), the Lead Remelt Facility (Study Area 19), the Red Water Ditch (Study Area 21), and the Beaver Pond Drainage System (Study Area 27).

The western edge of AAAP is adjacent to the Coosa River; groundwater flow is predominantly to the west-northwest, toward the Coosa River. The residences located within two miles of the installation may use private drinking water wells, but none are downgradiant from the plant. The city of Childersburg utilizes deep wells for its municipal water supply, with the closest municipal well 2.2 miles south of the installation boundary. Approximately 65 percent of surface water drainage is conveyed by three drainage systems, all of which flow toward the Coosa River. Two of these are natural systems (Beaver Pond Drainage System and the Crossover Ditch) and the third is man-made (Red Water Ditch). Surface runoff from the southern and eastern side of AAAP is via Talladega Creek, which flows into the Coosa River. No defined streams flow easterly from AAAP (ESE 1986).

Contamination of the shallow aquifer in the Industrial Area has occurred as a result of the leaching of munitions compounds from the soils and sediments at AAAP. However, the existing groundwater data is too sketchy to determine the extent of this contamination. Additional monitoring is being planned to better define this problem (Edwards 1989). Therefore, this report will address the problems at AAAP by focusing on the existing data for soils and sediments. When the additional groundwater data become available, this report will be revised, if necessary.

2. SELECTION OF ARARs

Selection of ARARs is dependent on the hazardous substances present at the site, the site characteristics and location, and the actions selected for a remedy. Thus, these requirements may be chemical-, location-, or action-specific. Chemical-specific ARARs are health- or risk-based concentration limits set for specific hazardous substances, pollutants, or contaminants. Location-specific ARARs address such circum- stances as the presence of an endangered species on the site or the location of the site in a 100-year floodplain. Action-specific ARARs control or restrict particular types of remedial actions selected as alternatives for cleanup of the site.

2.1 CHEMICAL-SPECIFIC ARARs

The Superfund public health evaluation process is composed of two phases: 1) the baseline public health evaluation and 2) the development of health-based performance goals for proposed remedial alternatives. The process is fully described in the USEPA Superfund Public Health Evaluation Manual (SPHEM) (USEPA 1986). The first step in the baseline public health evaluation process at Superfund sites is the selection of chemicals of concern or "indicator chemicals". This procedure identifies the chemicals that pose the greatest potential public health risk at a site and is based

on site monitoring data, chemical toxicity information in the form of toxicity constants developed by EPA, and environmental persistence and mobility of the chemicals.

Chemical-specific ARAR's or "to be considered" (TBC) guidance values are subsequently selected for the development of health-based performance goals (i.e., cleanup levels for contaminated soil or groundwater) in the form of a baseline risk assessment. The methodology outlined in the revised SPHEM (USEPA 1989) or the Preliminary Pollutant Limit Value (PPLV) methodology of Rosenblatt and Small (1981) may be utilized to quantitate exposure pathways and risk to individuals from exposure via the pathways of concern at a particular site.

2.1.1 Indicator Chemicals

We have developed the list of indicator chemicals for soils at AAAP following the guidelines outlined in Chapter 3 of SPHEM (USEPA 1986) . Initially, a concentration-toxicity screening procedure, as outlined in SPHEM, was used to obtain a relative ranking of detected chemicals based on indicator score (IS). A microcomputer-based spreadsheet was used to automate the routine features of the procedure. The IS for each chemical was calculated as the sum of the representative concentration times the oral toxicity constant for soil. The most current toxicity constants used to derive the IS for each chemical were provided by the Environmental Criteria and Assessment Office, EPA, Cincinnati. These numbers are listed in the EPA Public Health Risk Evaluation Database (PHRED) (USEPA 1988a). The Indicator Chemical worksheets, which show the calculation of the indicator scores are presented in the Appendix.

The top-scoring chemicals in the screening procedure, along with any detected chemicals for which toxicity constants are currently unavailable, were subsequently analyzed to establish a list of the chemicals posing the most significant health risks at the site. Final selection of indicator chemicals was based on evidence of human carcinogenicity, frequency of occurrence in environmental media, exceedance of acceptable intake values, exceedance of background levels, and environmental persistence and mobility.

Complete historical monitoring data for soil and sediments at AAAP were obtained from the Installation Restoration Data Management System maintained at USATHAMA. All monitoring data have been quality assurance/quality control validated by USATHAMA. When the additional groundwater monitoring data become available, the list of indicator chemicals will be reevaluated to incorporate this information. A total of 38 chemicals were detected in soil or sediment samples obtained from AAAP from 1980 to 1982 and 1985 to 1987.

Potential carcinogens and noncarcinogens were ranked by their indicator score, and three indicator chemicals (2,4-DNT, 2,6-DNT, and lead) were selected from the top-scoring compounds. Two additional munitions compounds (2,4,6-TNT and tetryl), for which toxicity constants are currently unavailable, were also selected as indicators because of

their occurrence in AAAP soils and sediments at high concentrations. In addition, 1,3,5-trinitrobenzene (TNB), a degradation product of TNT, was selected as it occurred in soils at seven different locations at AAAP; concentrations measured were relatively low, with the highest (3.92 mg/kg) occurring at the Flashing Ground (Study Area 16). A list of the indicator chemicals and supporting data is presented in Table 1.

The mixture of 2,4- and 2,6-DNT is classified as a B2 carcinogen (probable human carcinogen), as is 2,4-DNT alone (USEPA 1988b). The toxicity constant for 2,6-DNT listed in PHRED (USEPA 1988a) was developed based on its noncarcinogenic effects. However, recent studies have shown that the 2,6-isomer is a potent hepatocarcinogen (Leonard et al. 1983, 1987). 2,4,6-TNT has recently been classified by EPA as a Group C carcinogen (USEPA 1989a).

The primary areas of concern at AAAP are the Northern and Southern TNT Manufacturing Areas. ESE (1986) reports that approximately 65,300 m2

of soil in these areas are contaminated with the following munitions compounds: 2,4,6-TNT (with concentrations up to 7,900 fig/g), 2,4-DNT (with concentrations up to 16.0 fig/g), and 2,6-DNT (with concentrations up to 16.1 fig/g). The majority of contamination occurs in the upper 1.0 m of the soil. The DNTs are the most labile of these compounds with an estimated half-life of 6 years in the upper 1 ft of soil at AAAP (ESE 1986). However, 2,4,6-TNT undergoes photolysis and breaks down to the DNTs, TNBs, and dinitrobenzenes; consequently, these compounds are released into the surrounding soils. 1,3,5-TNB has been detected in soils in these study areas at concentrations up to 2.8 fig/g. The soils of the Flashing Ground (Study Area 16) are also contaminated with these munitions compounds and their degradation products. With the exception of 1,3,5- TNB, which was detected at a concentration of 3.9 fig/g, the compounds occur in lower concentrations in this study area.

Lead contamination is greatest in the soils of the Sanitary Landfill and Lead Facility (Study Area 3) and the Lead Remelt Facility (Study Area 19), with concentrations as high as 13,410 fig/g and 14,740 fig/g, respectively. Tetryl contamination is primarily confined to the soils of the Tetryl Manufacturing Area (Study Area 10), occurring at concentrations up to 13,700 fig/g.

Several other heavy metals, including nickel, copper, zinc, total chromium, and mercury, ranked among the top 10 noncarcinogens; however, they were not selected as indicators because they were detected infre- quently and at concentrations below guidance values for acceptable intake levels from soil Ingestion^.

^■Estimated using a Reference Dose (USEPA 1988b) and an assumed soil ingestion rate of 0.2 g/day for a 10-kg child (USEPA 1989b).

Table 1. Indicator Chemicals Selected for Alabama Army Ammunition Plant

Soil Sediment Indicator Representative Total Representative Total Scoring Concentration Number of Concentration Number of

Chemical Ranka (mg/kg) Occurences (mg/kg) Occurences

2,4-DNTb 5C

10d 1.6 43 1.2 12

2,6-DNTb 8d 2.2 14 0.6 5

Lead ld 356 310 52 63

Tetryl NAe 2442 7 1.3 1

l,3,5-TNBf NAe 1.5 11 1.3 2

2,4,6-TNTg NAe 569 45 3.8 9

aRank is based on the indicator score which is equal to the sum of the representative concentration times the toxicity constant across all media. bDNT - dinitrotoluene. cBased on carcinogenic effects. dBased on noncarcinogenie effects. eNA - Not available. Information concerning toxicity is presently insufficient; toxicity constant not available. fTNB - trinitrobenzene. STNT - trinitrotoluene.

During operations at AAAP, the man-made Red Water Ditch carried wastes from the primary munitions manufacturing areas to the Coosa River. Consequently, the sediments and spoil banks along this drainage are highly contaminated with these munitions compounds. Contamination from this system and from the soils of Areas 6 and 7 has migrated into the shallow aquifer underlying the Industrial Area. These compounds have been detected in groundwater at concentrations of 21,960 /xg/L for 2,4,6-TNT, 4,342 pg/L for 2,4-DNT, 1,085 jig/L for 2,6-DNT, and 4,494 j*g/L for 1,3,5- TNB. The Beaver Pond Drainage System is located between Areas 6 and 7 and mixes with the Red Water Ditch System. Both of these drainages flow into the Coosa River, thereby presenting the potential for off-post migration of these contaminants. In addition, the contaminated aquifer provides groundwater recharge to the surface waters of these areas (ESE 1986). The additional on- and off-post groundwater monitoring scheduled for this year should provide a better understanding of the contamination potential for this site.

2.1.2 Federal and State ARARs

There are at present no federal or Alabama state health-based ARARs that specify acceptable concentrations for cleanup of contaminated soils.

2.1.3 Other Guidance to be Considered

There are no available health-based guidance values for cleanup of nitroaromatics and metals in soils. However, Rosenblatt and Small (1981) have estimated acceptable concentrations of these compounds in soil that will result in no adverse health effects for several land use scenarios at AAAP. The basic equation utilized in the Preliminary Pollutant Limit Value (PPLV) approach of Rosenblatt and Small is:

_ BW x Dt Cs "iRxK '

where

Cs - the concentration in soil resulting in no adverse health effects following consumption of a particular pollutant, mg/kg;

BW - body weight, kg;

Dt - acceptable daily dose to humans, mg/kg/day;

IR - ingestion rate, kg/day; and

K - partition coefficient to reflect uptake from soil to matter ingested by man, unitless.

The PPLV methodology was applied to five pathways of exposure: ingestion of vegetables, meat (pork, beef, and venison), dairy products, and soil^; and dust inhalation. These pathways were then summed in various selected combinations to estimate the concentration in soil that would not cause adverse health effects in humans following exposure in various scenarios (residential housing, hunting, logging, etc.). Input parameters for the various pathways of exposure have been presented in the report by Rosenblatt and Small (1981). In the case of the nitroaromatics and metals, Dt was estimated from the best available information, whether in the form of a threshold limit value (TLV), ambient water quality criteria, or no observed effects level in animal studies.

2Rosenblatt and Small (1981) use a soil ingestion rate for children of 0.1 g/day. However, guidance from EPA in estimating exposures from contaminated soils recommends soil ingestion rates of 0.2 g/day for children aged 1 to 6, and 0.1 g/day for older age groups (USEPA 1989b).

EPA has listed health-based numbers in the form of Reference Doses (RfDs), acceptable chronic intakes, or carcinogen potency factors for several of the compounds found at AAAP (USEPA 1988b), and these values are presented here as "to be considered" (TBC) guidance for inclusion in the PPLV calculations for AAAP (see Table 2). Also listed in the table are the original Dt and PPLV values derived by Rosenblatt and Small (1981) for the most restrictive scenario, that of residential housing, and the soil detection limits for the compounds selected as indicator chemicals at AAAP (Weston 1988).

2.1.4 Conclus ions

Table 2 lists PPLV values for cleanup of contaminated soil as well as USATHAMA certified detection limits for the indicator chemicals at AAAP. Values "to be considered" for cleanup of contaminated soils at AAAP are underlined in the table. As can be seen from the table, the analytical detection limits for the DNTs exceed the PPLV concentration in soil estimated to be protective of human health assuming the most conservative exposure scenario (residential housing). Recalculation of the PPLV determined by Rosenblatt and Small (1981) using the more current RfD values would result in still lower PPLVs. Therefore, for these munitions compounds, in the absence of any federal or state-promulgated values for cleanup of contaminated soils, these detection limits should be used as TBC guidance.

In the case of lead and 2,4,6-TNT, the PPLV methodology of Rosenblatt and Small (1981) seems appropriate to use as TBC guidance, assuming that these values are adjusted to reflect the more current health-based RfDs and utilizing EPA-approved ingestion parameters. Although these revised PPLVs are not presently available, it appears that for lead, use of the revised PPLV will dictate cleanup levels, and for 2,4,6-TNT, the detection limit will be the appropriate cleanup level.

Tetryl and 1,3,5-TNB do not have any more current health-based values to use as guidance in estimating PPLVs, and so the PPLVs reported by Rosenblatt and Small (1981), which are higher than the analytical detection limits, are all that are available to determine cleanup levels for contaminated soils. Adjustment of these PPLVs by assuming a child's soil ingestion rate of 0.2 g/day rather than 0.1 g/day might reduce them somewhat, but they will still in all likelihood be higher than the detection limits.

Table 2. To Be Considered (TBC) Guidance for Cleanup of Contaminated Soils at Alabama Army Ammunition Plant

Indicator Chemical

Dt* (mg/kg/day)

USEPA DoseD

(mg/kg/day) PPLVC

(mg/kg) Detection

Limit (mg/kg)d

2,4-DNT 3.2 E-05e 1.5 E-06f 0.03 0,424

2,6-DNT 3.2 E-05 NAS 0.03 0.524

Lead 8.0 E-03 1.4 E-05h Ul 0.1771

2,4,6-TNT 1.4 E-05 5.0 E-04J 0.013 0.456

Tetryl 1.8 E-03 NA U. 0.731

1,3,5-TNB 5.8 E-03 NA 5.5 0.488

acceptable daily dose as derived by Rosenblatt and Small (1981). "The dose for noncarcinogens which will result in no adverse health effects or for carcinogens which will result in one excess cancer in a million people following lifetime ingestion of contaminated soil. Preliminary Pollutant Limit Value (Rosenblatt and Small 1981). dUSATHAMA Certified Method 11W12 using HPLC (Vondrick 1989). eRead as 3.2 x 10"3. ^The daily intake that will result in one excess cancer in a million people following lifetime ingestion of contaminated soil. Derived from a carcinogen potency factor (See footnote 3 below) . SNA - not available. acceptable Intake Chronic (AIC) (USEPA 1986). iuSATHAMA Certified Method using a graphite furnace (Vondrick 1989). ^Reference Dose (USEPA 1989b).

32,4-DNT is considered by EPA to be a Group B2 carcinogen. An oral carcinogen potency factor of 6.8 E-01 (mg/kg/day)"1 is available for DNT (USEPA 1988b). A dose of 1.5 E-06 mg/kg/day would result in one excess cancer among one million persons from incidental exposure to 2,4-DNT in the soil (an excess cancer risk of 1 x 10"6), derived in the following fashion:

10"6 Dose (mg/kg/day) -

qi* (mg/kg/day)

where

10"6 - selected risk level; q\ - oral carcinogen potency factor.

2.2 LOCATION-SPECIFIC ARARs

Location-specific ARARs set restrictions on remedial action activities depending on the characteristics of a site or its immediate environs. Much of the information regarding characteristics of the AAAP was provided by officials of the State of Alabama. Table 3 lists location-specific ARARs as discussed below.

2.2.1 Caves, salt-dome formations, salt-bed formation, and underground mines

The plant is underlain by dolomites and limestones of the Knox Group of Cambro-Ordovician Age. Both rock types are carbonated rocks which could be subject to cave formation (Osborne 1989). There are no salt- bearing units within the Knox Group, and salt domes and underground mine formations are not present (Osborne 1989). Kymulga Cave and Desota Caverns in Section 12, Township 20, are located within a few miles of the plant (Alabama Geological Survey 1988). The U.S.G.S. map of sinkhole- prone areas in Talladega shows two sinkholes within the present boundaries of the plant; one of the sinkholes has a maximum dimension greater than 0.2 mile (Alabama Geological Survey 1977). Construction projects in this area encountered sinkholes during 1978 (USATHAMA 1978).

Areas underlain by limestone are subject to cave formation and sinkhole development. Therefore, if any remedial action alternatives are contemplated in these areas, the Resource Conservation and Recovery Act (RCRA) regulations found in Table 3 may be relevant and appropriate.

2.2.2 Faults

Based on discordant structural orientations, a pre-Holocene thrust fault may be present approximately 2 miles south of the southern boundary of the plant (Alabama Geological Survey 1988). Although the existence of this fault appears likely, it is not visible in the outcrop. The area is very complex structurally, and both isoclinal folds and small-scale faults have been seen in outcrops along the west bank of the Coosa River in Section 30, Township 19 South, Range 3 East (Osborne 1989). Also, rocks in the Lambert quarry of Section 5, Township 21 South, range 3 East contain abundant upright chevron folds cut by steep ancient (pre-Holocene) faults (Alabama Geological Survey 1988). There are no reports of any recent movement of any faults in this area, so it can be concluded that the faults in the AAAP are stable (Osborne 1989).

2.2.2 Wilderness areas, wildlife refuges, and scenic rivers

The west boundary of the Talladega Division of the Talladega National Forest is approximately 15 miles to the east of AAAP. The Hollins Wildlife Management Area is located in this area of the Talladega National Forest. The Cheaha Wilderness is located approximately 40 miles to the northeast of the installation, within the Talladega National Forest. However, there are no wilderness areas, wildlife refuges, or scenic rivers inside the Depot (Brown 1989).

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2.2.4 Wetlands and floodplains

The majority of the surface runoff from AAAP drains either west or southwest into the Coosa River (USATHAMA 1978). A small portion of the southern and eastern side of AAAP drains toward the Talladega Creek, a tributary of the Coosa River. Extensive wooded swamp and open pond areas have developed in the drainage systems at AAAP since the beginning of demolition activities in 1973, primarily as a result of damming of drainways by beaver (Garland 1989). Beaver Pond and various watering ponds found at AAAP are actively being utilized by beaver and other animals.

Information concerning identification and location of wetlands is not available at this time from the U.S. Fish and Wildlife Service nor the Alabama Department of Conservation and Natural Resources (Raoscigno 1989; Hayden 1989). If remedial actions are contemplated that would impact the wetlands areas, a wetland installation assessment should be implemented (Hayden 1989).

Floodplains exist near Talladega Creek and near the Coosa River. The Talladega Floodplain Map indicates areas in the 100ryear floodplain near the southern portion of the plant adjacent to the Southern Railway Highway (FEMA 1988a). On the western side of the facility near the Coosa River some areas are subject to flooding on both sides of State Highway 225 (Wright 1989). In addition, part of the installation appears to be in the floodplain further north in an area west of Highway 235 and East of the Seabord Coastline Railway, (Wright 1989). Along the Coosa River there are floodplains on both sides of Ordnance Road, to the east and north junction of Talladega Creek with the Coosa River (Wright 1989; FEMA 1988b).

If any remedial actions are contemplated that would impact the wetlands or floodplain areas, the regulations found in Executive Order (E. 0.) 11990, the Clean Water Act § 404, E. 0. 11998, and 40 CFR 264.18(b) may be ARARs (See Table 3). In addition, remedial activities impacting any of the wildlife found on the installation may be subject to regulations found in the Fish and Wildlife Coordination Act (Table 3).

2.2.5 Historic sites and archaeological findings

There are 17 known archaeological sites within the immediate vicinity of the plant and many more within a few miles of the ordinance site (Oaks 1989). Of the known archaeological sites, 5 are potentially eligible for the National Register of Historic Places. The other sites would require further testing to determine eligibility (Oaks 1989).

There has not been a historic structure survey for this area and therefore no known structures that are listed on the site are eligible for the National Historic Register of Historic Places. The possibility for eligible structures does exist and the plant itself should be evaluated according to Alabama Historical Commission staff (Oaks 1989). If any remedial action is taken that would affect the preservation of any

12

archaeological findings at AAAB the National Archeological and Historical Preservation Act may be ARAR (See Table 3).

2.2.6 Rare, threatened or endangered species

A large variety of fauna and flora can be found in Talladega and Calhoun Counties. Vertebrate species include 27 amphibians, 46 reptiles, 192 birds, and 48 mammals (USATHAMA 1978). The red-cockaded woodpecker, Picoides borealis (vieillot) is listed as an endangered species by the United States Department of the Interior (USATHAMA 1978) and the state of Alabama (Mount 1986). If any remedial action is taken that would destroy this species or adversely modify its critical habitat, regulations found in the Endangered Species Act of 1979 may be considered ARARs (See Table 3).

13

2.3 ACTION-SPECIFIC ARARs

Action-specific ARARs are usually technology- or activity-based requirements or limitations on actions taken with respect to hazardous wastes. These requirements are triggered by the particular remedial activities that are selected to accomplish a remedy. For site activities that are in the RI/FS stage, a multiplicity of action-specific ARARs will apply to the remedial alternatives under consideration. Additionally, if the remedial alternative that has been selected involves sequential integrated actions, the design and implementation of each step will be governed by action-specific ARARs. Certain ARARs represent hybrids between chemical-, location-, and action-specific ARARs. These hybrid ARARs involve an action taken with respect to a specific constituent or location. Effluent discharge limits or air emission standards are considered hybrids between action-specific and chemical-specific ARARs because an action (i.e., a discharge) is taken with respect to a chemical.

As discussed in the introduction, AAAP was involved in the production of nitrocellulose, TNT, and tetryl. Chemical intermediates used in the manufacturing of these explosives, including aniline, diphenylamine, dinitrotoluene (DNT) and dimethyl aniline were also produced. Residues, off-specification materials, and wastewaters from these production activities were stored and disposed of at AAAP in the section delineated as Area B. Certain portions of Area B are contaminated with tetryl and TNT to such an extent that these soils are characteristically reactive (D003) under RCRA. Additionally, widespread low concentration contamination of soils and groundwaters by nitramines and nitroaromatics exists. The Red Water Storage Basin (Study Area 5) and Red Water Ditch (Study Area 21) received wastewaters and sludges from TNT manufacturing listed as K047 and K044, respectively. The majority of the reactive soils occur in the vicinity of the Red Water Ditch (spoil banks area) as a result of dredging the sludge from the ditch and basin. Under 40 CFR 261.3, any solid waste derived from the treatment, storage or disposal of a listed hazardous waste remains that listed waste. The residues, sludges, and wastewaters that were placed in the basin and ditch met the listing criteria at the time of placement and, therefore, the contaminated sediments derived from that activity are considered RCRA-listed wastes. The fact that certain of these residues no longer exhibit the characteristic of reactivity is irrelevant to the determination that the listing is applicable because the wastes were not mixed to eliminate the characteristic at the time of generation or placement in these areas. Under RCRA, the listing remains applicable unless the sediments are delisted.

Aniline and related organics were manufactured in Study Area 8. Residues from the manufacturing operations were disposed of in the Aniline Sludge Basin (Study Area 9). Sampling results in the RI/FS document do not include aniline or its manufacturing intermediates among the indicator chemicals for this study area. It is suspected that the residues disposed of in the sludge basin met the RCRA listings K083, K103, or K104 for certain process residues and wastewaters from aniline production. If the wastes disposed of in this basin met the listing criteria, the soils, sediments, or residues would be considered RCRA-listed wastes. For the

14

purpose of this document, the listing criteria is assumed to be met.

AAAP was proposed for listing on the NPL in October 1984 and fina- lized in July 1987. As a result of listing on the NPL, the remediation at AAAP must comply with ARARs derived from federal and state environmental laws. Although on-site treatment at NPL sites is exempt from permit requirements, the substantive standards derived from environmental laws may continue to apply as ARARs.

Several remedial actions for the soils and groundwaters of Area B were explored in the RI/FS document (ESE 1987). These alternatives included (1) off-site treatment and/or disposal, (2) removal of soils, etc., followed by on-site disposal in a secure landfill, (3) removal of soils for on-site incineration combined with extraction treatment and injection of groundwater, (4) capping of contaminated zones and (5) no- action. Action-specific ARARs for the first four alternatives are provided in Tables 4 through 7. Each alternative is further defined in subsequent sections.

The remedial actions that were explored in the RI/FS satisfy the prerequisites of several environmental laws. Every alternative except for the no-action plan consists of moving and treating the RCRA-listed wastes, which triggers the jurisdictional criteria of RCRA for generation, treatment, and disposal of a RCRA-listed waste. The jurisdictional criteria for discharges to the surface waters of the United States are met under certain alternatives and invoke requirements pursuant to the Federal Water Pollution Control Act (FWPCA). Additionally, the alternative of groundwater extraction, treatment, and injection involves requirements of the Underground Injection Control (UIC) program of the Safe Drinking Water Act.

2.3.1 Preliminary Decontamination Activities

Prior to initiation of any of the five studied alternatives, preliminary decontamination activities are planned for portions of Area B. These actions involve removal of the most severe contamination to allow flexi- bility in the cleanup approach and ensure safe work zones for remedial personnel. These preliminary decontamination actions include removal and flashing of contaminated sewer lines and spoil bank residues. Removal of friable asbestos contained in rubble piles will also be performed in the preliminary activities.

Requirements for open burning of explosives are found under RCRA interim status standards for thermal treatment (40 CFR 265.370 et seq.). Permitting standards for miscellaneous units (40 CFR 264.600 et seq.) are also applicable to open burning of waste explosives. The interim status standards establish requirements for waste analysis, inspection, operation and closure.

Under the general waste analysis requirements of 40 CFR 265.13, the sampling plan must ensure that the data will be representative and account for possible variations in the waste. In addition to the general waste

15

analysis requirements, the thermal treatment operator must determine the BTU sulfur and halogen content of the waste. Concentrations of lead and mercury must be determined unless documented evidence exists to indicate these constituents are not present. At AAAP, it is likely that it can be demonstrated that mercury is not present. These requirements are considered applicable to flashing the spoil pile residues and sewer lines because the type of activity, type of waste, and jurisdictional prerequisite of treating RCRA wastes after 1980 are met.

Inspection of all operating equipment, ancillary equipment, process monitoring and control instrumentation, emission control systems, and the plume are required during thermal treatment or on a daily basis. Emer- gency shutdown systems and alarms must be inspected daily to ensure proper operation. Due to the anticipated nature of the flashing operation, many of the requirements cannot be directly applied. It is expected that the flashing will be conducted with portable devices such as "flame throwers" or torches. For these systems, daily inspection of the fuel systems, igniters, piping, valves, nozzles, and instrumentation (pressure or flow gauges) would be considered applicable. Inspection of the treatment zone prior to operation would be considered appropriate. Additionally, plume monitoring for changes to opacity and color during treatment is considered an applicable requirement. Maintenance of inspection or operating logs would not be considered ARARs because these RCRA standards are administrative in nature.

Three operating requirements are established for thermal treatment (40 CFR 265.370 et seq). These include; (1) maintenance of steady state conditions during the treatment event, (2) location of the thermal treatment activity at a minimum distance from other properties, and (3) operation in a manner that protects human health and the environment. The requirement for steady state operation may be waived for batch operations such as the flashing activities that will be conducted at AAAP. Separa- tion distance requirements are based upon the mass of explosive material per treatment event. These requirements are inherently met by the flashing activities at AAAP. However, a separation distance equal to the minimum value specified in 40 CFR 265.382 (670 ft) is usually maintained between the open burning/open detonation (OB/OD) treatment zone and any other structure. Operation in a manner to protect human health and the environment is subsequently discussed in conjunction with general environmental performance standards for miscellaneous units. The waivers from steady state performance and distance standards are considered to be applicable requirements.

Althouth permits are not required for on-site remedial actions at NPL sites, the substantive standards related to the specific activity may formulate ARARs. Permit standards for miscellaneous units, including thermal treatment, are codified in 40 CFR 264, Subpart X. These standards require location design, operation, and closure of the unit in a manner that is protective of human health and the environment. Unlike other RCRA units where the general performance objectives are achieved by specified design standards, only generalized environmental performance standards are applied to miscellaneous units. The general environmental performance

16

Standards require that the owner demonstrate prevention of releases to air, surface waters, or subsurface media that could have adverse effects on human health and the environment. In demonstrating compliance with these standards, the operator must consider both waste and media characteristics. For example, the demonstration for subsurface media must consider waste characteristics, the units hydrogeologic characteristics, ground water quality and use, relative location of groundwater withdrawal wells, and risks to plant, animal or human receptors. Eleven similar factors must be considered to demonstrate compliance with the surface water performance standard. Factors for the air performance standard include waste characteristics, plume characteristics, reliability of the proposed treatment, atmospheric conditions, and the existing air quality.

The Endangerment Assessment (EA) performed in conjunction with the RI/FS generally meets the requirements of the Subpart X general environmental performance standards. However, compliance with this ARAR would require tailoring the EA to the flashing activity. Additionally, air emission factors would need to be considered to demonstrate compliance with that performance standard. Demonstration that this standard is met is usually achieved by instantaneous plume dispersion modeling such as the PUFF or INPUFF models. During detonation, the majority of energetic materials are converted to N2, H2O, and CO2• For example, alkyl nitrates, such as nitroglycerin, yield <0.15 lb of CO/lb of energetic material with the remainder converted to N2, H2O, and CO2. Aryl nitrates, such as TNT or tetryl, release some N0X during combustion. For example, during burning of TNT, -0.06 lb of CO and -0.16 lb of N0X are emitted. This type of mass balance data is generally input to the gaussion dispersion models to compare predicted airborne concentrations with National Ambient Air Quality Standards (NAAQS) at downwind locations. Thus, compliance with this performance standard will satisfy ARARs that are derived from both RCRA and the Clean Air Act (CAA).

Additional permit conditions that are generally applied to miscellaneous units are requirements to meet the general waste analysis, security, inspection, personnel training, and preparedness/prevention standards of 40 CFR 264, Subparts B and C. Waste analysis requirements include development of sampling procedures, frequencies, and analytical protocols for the parameters previously described. Security requirements include posting and the use of barriers to prevent unauthorized entry. Inspection and maintenance of emergency response equipment, operating equipment, and monitoring equipment are required by both 40 CFR 264.15 and 40 CFR 264.33. In particular, fire control equipment will need to be properly maintained and on hand during flashing operations.

Maintenance of spill control equipment, alarms, or aisle space would not be considered as ARARs because these items are not inherent to the flashing operations. Personnel training requirements for remedial activities are mandated by Occupational Safety and Health Administration (OHSA) standard 1910.120. It is recommended that personnel involved directly with flashing operations be provided additional specialized training in the use of the operating equipment specific to the activity and the unique hazards of the work. Although the documentation required

17

by many of the general facility standards (i.e., operation logs, inspection logs etc.) are administrative and, therefore, not ARARs, the conduct of these activities is considered relevant and appropriate. The remaining general facility standards of 40 CFR 270 (i.e., spill prevention procedures, procedures for loss of utilities, actions in the event of water supply contamination) bear no relation to the activity and, therefore, are not considered ARARs.

Upon termination of their active life, thermal treatment units must close by decontamination of equipment and facilities, removal of the waste, removal of residuals, and certification of closure. Although completion of the initial decontamination might be considered to cor- respond to closure, the activity is a part of a total remedial action, that upon completion, is intended to attain levels of control that are protective of human health and the environment. Thus, it is considered probable that closure requirements could be waived as ARARs. Under this provision (CERCLA § 121) the operational based requirements might also be waived, but their removal as ARARs is considered less likely.

The other activity that will be performed as part of the initial decontamination activity is removal of rubble piles that contain friable asbestos. The potential ARARs for this activity are the National Emis- sions Standards for Hazardous Air Pollutants (NESHAPs) derived from the CAA and certain OSHA requirements. It is considered possible that the de minimis emission rate of 14 lb/year will be exceeded by removal actions. Thus, the asbestos must be maintained in a thoroughly wet condition during removal. Removed material must be double bagged and these packages must be properly labeled in accordance with OSHA requirements. Although the bag type is not specified, the recommended disposal bag is constructed of 6-mil polyethylene. No sharp objects should be placed in the bags and all excess air should be removed. The bagged material should be loaded in fiberboard drums that are also labeled per OSHA requirements. The waste material should be transported for disposal in a dedicated cell in an approved solid waste landfill and covered with 6 in. of compacted soil on a daily basis. No visible emissions are allowed during removal, collection, or disposal.

Additionally, airborne concentrations must be monitored during removal actions to ensure compliance with OSHA standards, NESHAPS, and Alabama Air Toxics Limits. The Permissible Exposure Limit (PEL) for asbestos is 0.2 fibers/cm . State air standards are normally based on the Threshold Limit Value (TLV) of <2 fibers/cm3.

ARARs applicable to the initial decontamination actions are sum- marized in Table 4.

2.3.2 Off-Site Alternatives

Two off-site alternatives were considered in the RI/FS. Both alternatives involve excavation of soil and sediments for off-site management and extraction of groundwater for treatment at an off-site

18

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Publicly Owned Treatment Works (POTW). In both alternatives, soils and sediments will be excavated to meet the soil cleanup levels listed in Table 2. After excavation, in Alternative 1A, the soils would be transported to a RCRA-permitted landfill for disposal. In this alternative, groundwater would be extracted and transported for treatment at an off- site POTW. The second off-site alternative (Alternative IB) differs from the first option only in that the soils and sediments would be incinerated.

The first phase of this remedial action is the excavation of the contaminated soils in Area B. These activities will require the development of surfaces suitable for vehicular traffic. It is known that limited excavation, movement of soils, site grading, and site cleaning activities will be required. As a result of these actions, requirements from two environmental statutes are considered potential ARARs (see "On-site construction", Table 4).

Under § 316 of the Water Quality Act (WQA) of 1987, states are required to provide to EPA an assessment that identifies those bodies of water that do not attain Ambient Water Quality Standards (AWQSs) as a result of nonpoint source pollution. In conjunction with this effort, states must develop and submit to EPA Best Management Plans (BMP) designed to reduce the impact of pollutants from these nonpoint source discharges. Under WQA, the state assessment reports and BMPs were to be submitted to EPA by August 1988.

Surface waters in the vicinity of the construction site will need to be monitored to identify potential impacts from this nonpoint source (construction) activity. The relevant monitoring parameters for such activities generally include total suspended solids (TSS), total dissolved solids (TDS), biochemical oxygen demand (B0D5), and color. Additionally, construction of control devices such as runon diversion trenches, berms, and/or settling basins should be considered to reduce impacts from site- related activities. Such activities would be considered applicable only if the state identified the receiving stream as not in compliance with AWQSs due to nonpoint source pollution. However, such requirements are relevant and appropriate because the affected media, pollutants of concern, activities, and objectives within Sect. 316 of the WQA and those related to this stage of the remedial action are sufficiently similar.

Airborne pollutants will also result from these construction activities. The primary concern is elevation of particulate concentrations resulting from earth-moving and site-grading activities. Monitoring for particulate levels during site construction activities is generally required for any large-scale construction operation. Thus, this monitoring standard is considered relevant and appropriate due to its general application. The particulate concentrations are determined by placing PM-10 samplers at the property boundaries. The NAAQSs for particulates are 50 /*g/m3 per arrival and 150 /xg/m3 per 24-hour period. AAAP is responsible for meeting these standards, although such standards are rarely enforced. Generally, procedures for control, such as spraying down roads for dust suppression, will be sufficient to meet the standards

31

during the construction phase.

The next procedure in this action is transporting the soils off-site for treatment (see "Transportation", Table 4). Removal of the RCRA-listed wastes (soils and sediments) from the Aniline Sludge Basin, Red Water Storage Basin, Red Water Ditch or Spoil Banks is considered new generation of hazardous wastes. Other soils or sediments that are excavated will not be hazardous waste unless these are characteristically hazardous by reactivity. Any generator that transports or offers for transportation, hazardous waste for off-site treatment, storage or disposal, must prepare a manifest. The waste must be packaged in accordance with Department of Transportation (DOT) regulations codified in 49 CFR Parts 175, 178, and 179 (see Table 4). These requirements are considered ARARs for the hazardous waste soils as AAAP meets the prerequisites as a generator of a hazardous waste. In addition to the manifest and pretransport requirements detailed in Subparts B and C of 40 CFR 262, standards for labeling, marking, and placarding that are stated in 49 CFR Part 172 must be met.

Under 40 CFR 262.34, generators may accumulate waste on-site for up to 90 days in a nonpermitted storage facility. Although direct loading to transport vehicles is possible, it is considered probable that accumulation or storage of the waste may be required. Accumulation areas must comply with the interim standards of 40 CFR 265, Subparts C, D, and I. These standards are similar to those found in 40 CFR 264, but the latter are more stringent, and thus are listed in Table 4. Accumulation areas must maintain alarm or communication systems, emergency response equipment, spill control equipment, and decontamination equipment. Sufficient aisle space for operations, inspections, and emergency response must be provided. Standards codified in 40 CFR 265, Subpart D require development of a contingency plan that establishes an emergency response coordinator, identifies response equipment, and establishes response procedures. The equipment, aisle space, and inspection requirements from 40 CFR 265, Subpart C, are considered ARARs because these are design and operating standards. Contingency plans are administrative requirements that would not normally be considered ARARs but were retained because such documents are usually prepared as a matter of course for remedial activities.

Interim accumulation of RCRA-listed wastes in containers or tanks invokes requirements of 40 CFR 265, Subpart I or J, respectively. If accumulation is performed in containers (see "Container storage, on-site", Table 4), the primary requirements include the following:

• containers must be compatible with the waste, • incompatible waste must be segregated and may not be placed in

the same container, • containers must be in good condition and managed to prevent

spill or rupture, • containers must remain closed except for placement or removal of

waste, • containers must be properly marked and labeled, and • containers must be inspected weekly.

32

Accumulation tanks must meet requirements of 40 CFR 265, Subpart J (see "Tank storage", Table 4). New tank systems must be designed to ensure structural integrity and prevent corrosive attack. Prior to use, tank system components must be visually inspected for defects, the installation must be certified and the system must be leak tested by a volumetric or nonvolumetric technique. Accumulation tanks must be provided with secondary containment equal to 100% of the volume of the largest tank within its boundary and be fitted with interstitial monitoring. Secondary containment provisions may be waived on the basis of alternate design, location, operating, and waste characteristics. Such a waiver would be considered likely if a covered top tank were used for accumulation of soils. Additional tank system requirements include daily inspection of all externally accessible portions of the tank system. The container and tank accumulation requirements are considered ARARs. Upon closure of the accumulation area, the general interim status closure performance standard of 40 CFR 265.111 must be met (see "Tank closure", Table 4).

If the soils are stored on-site for longer periods of time, certain additional standards become applicable. Facilities that store RCRA-listed waste in containers or tanks must comply with 40 CFR 264, Subparts B, C, D, E, G, and H. Requirements pursuant to Subparts E and H are administrative and are not considered ARARs. The preparedness and contingency plan requirements of Subparts C and D do not differ substantially from those previously discussed. Thus, the primary additional requirements derive from the 40 CFR 264, Subpart B, General Facility Standards.

Under the General Facility Standards (40 CFR 264.10 et seq.), container storage facilities are required to develop and maintain waste analysis plans, site security procedures, site inspection schedules, and provide personnel training. Although the documentation required by these standards is administrative in nature and, therefore, not ARARs, the conduct of these activities is relevant and appropriate.

The primary additional container storage facility requirements under 40 CFR 264, Subpart I include runon and runoff controls, an impermeable crack-free base that is sloped to minimize contact with free-standing liquids, and a containment system sized to contain 10% of the stored volume. These standards are detailed under "Container storage" in Table 4. Container closure standards (Table 4) appear in 40 CFR 264.178.

As an alternative storage system, a waste pile may be used for the staging operations (see "Waste piles", Table 4). Design and operating requirements are found in 40 CFR 264.251. Waste piles must be constructed with a single liner and leachate collection system above the liner. The liner and leachate collection system must be compatible with the waste constituents and must have sufficient strength to withstand operational stress, static pressure and climatic conditions. In addition to the liner/leachate collection system, waste piles must be provided with a runon control system designed for a 25-year, 24-hour flood event and provided with groundwater monitoring. During operation, the pile, control

33

systems, and leachate collection system must be inspected weekly. The liner system must be inspected during and after construction.

The liner/leachate and groundwater monitoring provisions may be waived if the design is an engineered structure that controls entry of runon and precipitation, provides inner and out layers of containment, and stores no free liquids. This design is most readily accomplished by a base that consists of compacted clay, a drainage bed, and an FML that is surrounded by berms or walls and provided with a roof.

For alternative 1A, the landfill to which AAAP transports the hazardous waste must meet the minimum requirements of 40 CFR 264. The facility in Emelle, Alabama where AAAP plans to ship the waste meets these standards. Additionally, under Sect. 121(d)(3) of CERCLA, off-site disposal facilities must be in compliance with requirements established pursuant to RCRA 3004(u), 3004(v), or 3008(h).

The land disposal requirements from 40 CFR 268 will pertain to certain wastes removed from AAAP (see "Off-site landfill", Table 4). Soils and sediments from the Red Water Storage Area (Area 5) and Red Water Ditch (Area 2) meet the 40 CFR 261.32 listings K044 and K047. Under the "first third" land disposal restrictions the treatment standard for these wastes is no disposal. Thus, these soils/sediments must be thermally treated and delisted prior to land disposal. 40 CFR 264.600 addresses thermal treatment units.

Soils and residues removed from the Aniline Sludge Basin (Study Area 9) are suspected of meeting the 40 CFR 261.32 listings of K083, K103, and/or K104. Land disposal restrictions for these wastes are codified in 40 CFR 268.43 and are specified as the Constituent Concentrations in Waste (CCW) for K103 and K104. The Best Demonstrated Available Technology (BDAT) for K083 is no disposal. Thus, if the K083 listing is appropriate, these soils must be incinerated or thermally treated and delisted prior to disposal. If the K103 and K014 listings apply, the soils must be treated to below the 40 CFR 268.43 CCW limits prior to land disposal. The CCWs for K103 and K104 nonwastewaters presented below would be the applicable land disposal restriction criteria.

Contaminant Concentration (ppm)

Aniline 5.6 Benzene 6.0 2,4-Dinitrophenol 5.6 Nitrobenzene 5.6 Phenol 5.6 Cyanides 1.8

Alternative IB differs from Alternative 1A in that the soils and sediments will be incinerated off-site (see "Off-site incineration", Table 4). All of the construction or transportation and storage standards discussed for Alternative 1A and appearing in Table 4 continue to apply

34

for the Incineration alternative. Also applicable are CERCLA-based standards for off-site treatment units in compliance with RCRA 3004(u).

The off-site incineration alternative offers the advantage that thermal treatment followed by delisting is required for certain 40 CFR 268 restricted wastes. Additionally, incineration is likely to achieve the CCW limits for other restricted wastes derived from AAAP. Incineration ARARs are discussed in conjunction with the on-site incineration alternative in Sect. 2.3.4.

The final phase of this remedial action alternative involves the treatment of the extracted groundwater by a POTW. At present, there are no ARARs applicable to the extraction wells. However, certain standards must be achieved before the POTW can treat the groundwater. Discharge to a POTW (see Table 4) is considered an off-site activity. Off-site actions must comply with all legally applicable requirements including permit and administrative conditions.

The National Pretreatment Program, authorized under CWA §307(b), controls the indirect discharge of pollutants to POTWs. For the effluent to be acceptable to the POTW for treatment, the discharge of pollutants in the effluent that pass through the POTW without treatment, interfere with POTW operation, contaminate POTW sludge, or endanger health/safety of POTW workers, is prohibited.

In addition to the general prohibition on discharges that pass through or interfere, 40 CFR 403.5 establishes specific prohibitions that preclude certain discharges to POTWs. These specific prohibitions are provided in Table 4. Enforcement of the specific prohibitions varies among municipalities. The discharge must also comply with local POTW pretreatment programs, including POTW-specific pollutants, permit requirements, and monitoring requirements (40 CFR 403.8).

RCRA permit-by-rule requirements are triggered if the POTW receives hazardous wastes by truck, rail, or dedicated pipe (40 CFR 270.60). The widely dispersed contamination at AAAP precludes any determination that contaminated groundwater derives directly from treatment, storage, or disposal of listed wastes. If the wastewaters are determined to be hazardous waste, then the prerequisite is met and the permit-by-rule regulations are deemed applicable. In summary, these include compliance with their NPDES permit, RCRA notification requirements, the manifest system, and reporting requirements. The influent must meet all federal, state, and local pretreatment standards. If the POTW is operating under an NPDES permit issued after November 8, 1984, including renewed permits, the POTW must also comply with the corrective action requirements under RCRA 3004(u).

2.3.3 On-Site Landfill/Groundwater Treatment Alternative

The on-site landfill alternative involves excavation of soils/ sediments contaminated with explosives and lead to achieve soil cleanup levels and placement of these residues in an on-site landfill. Table 5

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40

lists the ARARs for this alternative. Soils/sediments contaminated only with lead will be removed from Area B, and depending on the EP Toxicity tests, may be placed in an on-site sanitary landfill. Contaminated groundwater will be extracted from Area B and treated on-site using carbon adsorption. The treated effluent will then be reinjected, upgradient of the extraction well network, and the spent carbon will be deposited in the secure landfill.

Prior to construction or operation of the disposal or treatment units required by this alternative, construction activities will be required to stage and place the equipment, establish utilities, provide piping runs, and establish work zones for the purpose of decontamination, site management, and monitoring. The ARARs for "Excavation" and "On-site construction" were discussed in Sect. 2.3.2 and are listed in Table 4.

Contaminated soils will be placed into the landfill constructed on- site. A portion of the soils to be landfilled are considered listed hazardous waste (K044, K047, K083, K103). Other soils contain several 40 CFR 261, App. VIII, hazardous constituents, such as DNT, nitrobenzene, or lead, although these soils do not appear to be characteristically hazardous. Removal of the listed soils and placement in the new secure landfill constitutes generation and disposal. Thus, a jurisdictional prerequisite is established that requires the landfill to meet RCRA standards for design, operation, maintenance and closure phases. These standards are detailed in 40 CFR 264, Subparts F, G, and N, and are considered ARARs for this action.

The Hazardous and Solid Waste Amendments (HSWA) established minimum technological requirements for new landfills (40 CFR 264.300 et seq.; see "Construction of new landfill on-site", Table 5), including the use of two or more liners and a leachate collection system above and between the liners to detect any leaks. An intensive quality assurance (QA) program is required to ensure proper construction of the synthetic liner. Standard engineering practice requires removal of a statistical number of samples of the welds for destructive inspection to ensure their integrity.

The leachate collection systems must be fed to a central collection sump and leachate treatment system. Inspection of the leachate collection system for the presence of free liquids and treatment of collected leachate will be required in both the active life and postclosure period. To prevent damage to the landfill, a runon and runoff control system to manage the water volume resulting from a 24-hour, 25-year flood event must be constructed and maintained (40 CFR 264.301).

During construction and operation, inspections for particulate matter, imperfections in the liner, improper operation of runon and runoff controls, ponding, liquids in the leachate collection system, and the structural integrity of the berms is required (40 CFR 264.303). In addition, berms must be constructed so that structural integrity is ensured by a slope of <30° and proper compaction during construction. The inspections are required weekly and after storm events.

41

During operation, all ignitable or reactive waste must be rendered noncharacteristic prior to placement in the landfill. Under the HSWA provisions, bulk hazardous or nonhazardous free liquids may not be placed in the unit (see "Placement of liquid waste in landfill", Table 5). Containerized waste must not have free-standing liquids upon disposal. Thus, it is possible that certain soils will require addition of silicate solidification agents prior to disposal. As previously described, soils from Areas 5, 9, and 21 must meet the pretreatment standards prior to disposal. For those soils from Areas 5 and 21 the 40 CFR 268 restriction criteria is a "no disposal" standard and, therefore, these soils must be thermally treated and delisted prior to disposal (see "Placement of waste in land disposal unit", Table 5).

The general groundwater monitoring requirements found in 40 CFR 264.91-100 will apply. A minimum of one upgradient and three downgradient wells are required for the detection monitoring program specified by HSWA for new land disposal units. These wells should be located in the shallow low-yielding aquifer with the upgradient well positioned to be unaffected by the unit and the downgradient wells located at the waste management boundary. The aquifer must be sampled for depth, direction, and flow on an annual basis. During the first year of operation, a data base of background values for the National Interim Primary Drinking Water Stan- dards and other pertinent indicator parameters must be established from the upgradient wells. The other indicator parameters generally include total organic carbon, total organic halides, pH, specific conductance, and any 40 CFR 264, App. IX indicator chemical that may be reasonably derived from the facility.

Upon closure of the landfill (see "Closure with waste in place", Table 5), postclosure care must be provided for a minimum of 30 years. The landfill must be capped by a clay and FML cap less permeable than the bottom liners. Long-term maintenance must be provided for the runon diversion system, cover system, cap, groundwater monitoring system, leachate collection system, and leachate treatment system. Long-term monitoring of the waste containment system must also be provided (see "Capping", Table 7).

The next action will be the treatment of the groundwater in the carbon adsorption system. The standards that are potential ARARs for the treatment system are indicated under "Treatment unit" in Table 5. The standards typically applied to treatment systems are those for tank systems found in 40 CFR 264.190 et seq. (see "Tank storage", Table 4). Under 40 CFR 264.192, all new tank systems are required to provide structural integrity, compatibility with the waste, an assessment of the corrosion potential, and the required type of corrosion protection. Additionally prior to use, the tank system must undergo a visual inspection, certification of proper installation, and either a volumetric or nonvolumetric integrity test.

Further design and operating requirements for tank systems are provided in 40 CFR 264.193 through 40 CFR 264.195, including secondary containment, interstitial monitoring, and overflow prevention systems,

42

such as level controls, bypass systems, process flow controls, and process monitoring equipment. The final operating requirement for tank systems is that all externally accessible portions of the tank, ancillary equipment, and secondary containment must be inspected daily.

These design and operating requirements are applicable to the activated carbon columns, any holding tanks, and ancillary equipment employed in the treatment system if the groundwater contamination is considered to be derived from disposal of hazardous wastes. However, the diverse nature of the contamination at AAAP prevents determination that groundwaters are hazardous waste under the "derived from" rule since contamination may result not only from listed and characteristic waste but also from non-RCRA nitroaromatic contaminated soils. Thus, it is possible that the treatment system would not need to meet the RCRA tank rules.

During operation, spent activated carbon will be generated by the treatment unit. Accumulation or on-site storage of this waste will be required (see "Container storage" and "Tank storage", Table 4). If the spent carbon is considered derived from hazardous waste groundwater and is accumulated for <90 days, the applicable requirements are limited to the standards of 40 CFR 265, Subparts C, D, and I. These standards have been previously discussed in conjunction with accumulation of excavated soils (Section 2.3.2). Upon closure of the accumulation area, the general interim status closure performance standard of 40 CFR 265.11 must be met. If the activated carbon is stored on-site for longer periods of time, certain additional standards become applicable. These standards were previously discussed in Sect. 2.3.2.

Spent filter elements from the filtration component of the treatment system must also be stored or accumulated in accordance with these requirements.

Interim status closure requirements of 40 CFR 265.110 et seq. and the unit-specific closure requirements of 40 CFR 265.178 ("Container storage", Table 4) and 40 CFR 265.197 ("Tank storage", Table 4) are also considered applicable to the treatment system and storage facility. The general closure requirements require preparation of a closure plan that details all standards and procedures for waste removal, mitigation of runon, treatment of runoff, monitoring during closure, and that ensure safe handling. The plan must provide detailed descriptions of the methods used to decontaminate or dispose of contaminated structures, facility equipment, work zones, and equipment used for closure. Finally, the plan must provide a step-by-step procedure and corresponding schedule to achieve the elements of the closure action. The closure requirements of 40 CFR 265.178 for container storage do not exceed the general standards. Closure requirements for tank systems are codified by 40 CFR 265.197. For clean closure, these standards are essentially analogous to those for container storage with the added requirements to decontaminate the tank system and secondary containment, remove contaminated soils, and render the tank unfit for further use if it remains on-site. Decontamination of tank systems is usually accomplished by a combination of solvent rinses and steam cleaning. For tank systems without adequate secondary contain-

43

ment or that cannot remove all contaminated soils, landfill closure may be required (40 CFR 265.310). As before, the standards of 40 CFR Part 264 are listed on the tables.

The general performance standard for the extraction or injection wells is that their construction and operation not result in the contamination of an underground source of drinking water (40 CFR 144.12). This requirement applies to both Class I and Class IV wells (see "Underground injection of wastes and treated groundwater", Table 5).

After treatment in the carbon adsorption system, the water will be recharged to the groundwater (see "Underground injection of wastes and treated groundwater", Table 5). As defined by 40 CFR 144.6, Class IV wells are wells used by generators of hazardous waste or owners or operators of hazardous waste management facilities to inject hazardous waste into or above a formation containing an underground source of drinking water within one-quarter mile of the well bore. Operation or construction of Class IV wells is prohibited and allowed only for the reinjection of treated groundwaters as part of a CERCLA or RCRA cleanup action (40 CFR 144.13).

Effective August 8, 1988, the "first third" of RCRA listed waste were prohibited from land disposal. As previously indicated, these restricted wastes included K044, K047, K083, K103, and K104. However, land disposal via an injection well was not prohibited as of this effective date. Under 40 CFR 148.14, underground injection of K104 is prohibited as of August 1990 unless the pretreatment standard of 40 CFR 268, Sübpart D, is met prior to injection (see "Placement of waste in land disposal unit", Table 5). The standards for nonwastewater K104 were provided in Section 2.3.2. If any of the groundwater contamination could be directly attributed to disposal of K104 in the Study Area, then the groundwater would require treatment prior to reinjection to the K104 wastewater CCW limits indicated below:

• aniline - 4.5 ppm, • benzene - 0.15 ppm, • 2,4-dinitrophenol - 0.61 ppm, • nitrobenzene - 0.073 ppm, • phenol - 1.4 ppm, and • cyanides - 2.7 ppm.

2.3.4 On-Site Incineration/Groundwater Treatment Alternative

Under this alternative, soils/sediments contaminated with explosives or explosives and lead will be removed from Area B to meet the soil cleanup criteria listed in Table 2. Soils/sediments contaminated with explosives or explosives and lead will be treated in an on-site incinerator. Soils/sediments contaminated with lead only will be disposed in an on-site RCRA-designed landfill. On-site treatment of groundwater from Area B is the same as described under the preceding alternative, with the exception that the spent carbon will be incinerated or regenerated on-

44

site.

For this action, the excavation and construction requirements are the same as those discussed in preceding sections and presented in Table 4. Also for those soils that are considered RCRA-listed wastes (Study Areas 5, 9, and 21), the accumulation or storage requirements, the landfill standards, the land disposal restriction, and the pretreatment standards (BDAT) are the same for those in the preceding alternative (Table 5). If contaminated groundwater is considered as derived from RCRA-listed waste, the storage and treatment standards previously discussed are applicable. Incinerator ash from treatment of RCRA-listed soils and possibly spent carbon (if the derived-from criteria applies) must also meet these standards. For other soils and possibly activated carbon, which do not exhibit a hazardous waste characteristic, only sanitary landfill disposal is required (see "Construction of new landfill on-site" and other landfill regulations found in Table 5). However, it is assumed that only a single secure landfill would be constructed for practical reasons. Thus, this alternative differs from prior options only due to incineration activities.

For the incineration alternative, several requirements will have to be met during the installation, operation, and removal of the system. The potential ARARs for this activity derive from the incinerator standards of 40 CFR 264, Subpart 0 (see Table 6). These standards are considered applicable because the incinerator provides treatment to K044, K047, K083, K103, and K104 wastes.

In general, items such as the temperature, feed rate residence time, and fuel/air ratios are specified and monitored to ensure that a specified destruction and removal efficiency (DRE) is achieved. Operating limits for the waste feed system, particulate removal system, gas scrubber, and monitoring trains are specified to ensure that the gas exiting the incinerator will have a minimum of pollutants and will not violate any air standards.

The incinerator must be designed, constructed and maintained so that it can meet certain emissions standards. The principal organic hazardous constituents (POHCs) in the waste feed must be treated to the extent that a DRE of 99.99% is achieved. Based upon sampling results, the POHCs will include NB, TNT, TNB, and 2,4-DNT. Particulate emissions must be <180 mg/dry standard or when corrected for the amount of oxygen in the stack gas. In order to ensure that the incinerator meets these standards, the following waste analysis parameters should be monitored: viscosity, heat capacity, the presence of all 40 CFR 261, App. VIII hazardous constituents, halogens, sulfur, and volatile metals.

Periodic analysis of the feed to ensure that anomalies do not occur is relevant and appropriate. It is expected that feed analysis based on a statistical sampling program would be relevant and appropriate to detect feed variations, which can cause a change in the DRE.

45

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Feed analysis for certain volatile EP metals (As, Cd, Cr, Pb, and Hg) is considered appropriate. Additionally, the stack gas should be monitored for products of incomplete combustion (PICs), CO, N0X, S0X, and volatile EP metals. This is done to ensure that the incinerator is functioning properly with complete mixing and burning. These parameters will ensure that both the DRE and air standards will be met. At present, the AAAP area is in attainment for all National Ambient Air Quality criteria. For new sources, Prevention Significant Deterioration (PSD) review is required if the source emits greater than 250 tons per year of any criteria pollutant. Certain criteria pollutants (N0X, CO, TSP) will be emitted and it is possible that the PSD major source criteria will be violated. Modeling of incinerator emissions to confirm this estimate is recommended. None of the POHCs are on the National Emission Standards for Hazardous Air Pollutants, and, therefore, NESHAP standards need not be considered. It should be noted that poor operating characteristics may result in incomplete combustion of the nitroaromatics with attendant release of benzene or toluene, which are considered under NESHAPs. Additionally, for each waste feed type, a detailed set of operating conditions must be specified and monitored that generally includes: CO level, waste feed rate, combustion temperature, residence time, combustion gas velocity, excess fuel/air requirements, and parameters that initiate the feed cutoff system.

During the startup and shutdown of the incinerator, waste must not be fed into the incinerator unless the incinerator is operating within the specified conditions of operation. A system that automatically terminates the waste feed to the incinerator whenever operating conditions deviate from the established limits is required. The incinerator and its associated equipment must be subjected to thorough visual inspections on at least a daily basis and the emergency waste feed cutoff system and its associated alarms must be tested at least weekly. At a minimum, operational testing must be conducted at least monthly.

Under 40 CFR 264.340(b), incinerators that destroy waste that is listed in 40 CFR 261, Subpart D, solely for corrosivity, ignitability, or reactivity are exempt from all 40 CFR 264, Subpart 0, requirements except waste analysis and closure. Accordingly, if it can be demonstrated that the sediments, activated carbon, and associated free liquids are not EP toxic, none of the RCRA incinerator standards previously described are ARARs. Exhaust gas monitoring to ensure compliance with NAAQS and NESHAPs, however, is still considered relevant and appropriate.

At closure, all hazardous waste and hazardous waste residues must be removed from the site, including (but not limited to) ash, scrubber waters and scrubber sludges. The incinerator and all ancillary equipment must be decontaminated prior to removal. Decontamination rinses must be managed as hazardous waste (40 CFR 264.351).

2.3.5 Capping Alternative

Under this alternative, soils/sediments contaminated with explosives or explosives and lead will be removed from Area A to achieve applicable

50

requirements (unrestricted use criteria, i.e., PPLVs for explosives) and transported and placed in a newly constructed monitored containment structure located in Area B. Further, under this alternative, surficial soils and sediments contaminated with explosives, explosives and lead, and lead only in Area B will be covered with soil to isolate contaminants from direct contact.

The remedial actions for Area A have already been performed and did not include the transportation of any hazardous waste to Area B for disposal and treatment. Therefore, those actions under this alternative that pertain to the treatment of Area A soils were not performed but will be considered. Table 7 lists ARARs for this alternative.

For the capping phase of this action, the prerequisite for jurisdictional applicability is that the RCRA hazardous waste placed at the site after the effective date of the requirements, or placement of hazardous waste into another unit, will make requirements applicable when the waste is being covered with a cap for the purpose of leaving it behind after the remedy is completed. Thus, the capping regulations are not applicable; however, as the waste is a RCRA-listed hazardous waste and this action is similar to the storage, and disposal of hazardous waste, these requirements will be considered relevant and appropriate.

The general requirements for the capping action are set forth in 40 CFR 264.228 (surface impoundments), 40 CFR 264.258 (waste piles), and 40 CFR 264.310 (landfills). These requirements state that the cover must be designed and constructed to provide long-term minimization of migration of liquids through the capped area, function with minimum maintenance, promote drainage and minimize erosion or abrasion of the cover, and accommodate settling and subsidence so that the cover's integrity is maintained. Additionally, to keep water and leachate from collecting in the waste, the cap should have a permeability less than or equal to the permeability of any bottom liner system or natural subsoils present.

In the document Alabama Army Ammunition Plant Remedial Actions Final Report, all soils in Area A that were contaminated with hazardous waste had been treated to below levels which require treatment. However, these soils were considered hazardous waste based on being contaminated by listed wastes due to reactivity. Therefore, these ARARs would apply unless these wastes were delisted, which is an administrative procedure not required in ARARs. Even though they are administrative, the steps for delisting would be required to complete this action and would be considered relevant and appropriate.

2.3.6 No Action

For the no-action alternative, there are no action-specific ARARs.

51

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REFERENCES

Alabama Geological Survey, Tuscaloosa. 1988. State Geologic Maps.

Alabama Geological Survey, Tuscaloosa. 1977. Areas in Which Sinkholes Have Occurred or Can Occur in Talladega, County, Alabama.

Brown, J. 1989. Forestry Commission, U. S. Forest Service, Montgomery, Alabama. Letter to Rose Weaver, January 22, 1989.

Edwards, D. 1989. U. S. Army Toxic and Hazardous Materials Agency. Aberdeen Proving Ground, Maryland. Personal communication (301-671-3460).

Environmental Science and Engineering (ESE) Inc. 1986. Alabama Army Ammunition Plant Remedial Investigation, Final Report, Contract No.DAAKll- 83-D-0007. Gainesville, Florida. July, 1986.

Environmental Science and Engineering (ESE), Inc. 1987. Alabama Army Ammunition Plant Feasibility Study. Final Report. Contract No. DAAK11- 83-D-0007.

Federal Emergency Management Administration. 1988a. Floodplain Map (Panel 0125), Talladega County.

Federal Emergency Management Administration. 1988b. Floodplain Map (Panel 200), Talladega County.

Garland, W. 1989. Forestry Commission, U. S. Forest Service. Personal communication (205-848-3758).

Hayden, D. 1989. Alabama Fish and Wildlife, Wetlands Specialist. Personal communication (205-261-3469).

Leonard, T.B., M.E. Graichen, andJ.A. Popp. 1987. Dinitrotoluene isomer-specific hepatocarcinogenesis in Fischer-344 rats. Jj_ Nat. Cancer Inst. 79:1313-1320.

Leonard, T.B., 0. Lyght, and J.A. Popp. 1983. Dinitrotoluene structure- dependent initiation of hepatocytes in vivo. Carcinogenesis 4(8):1059-1061.

Mount, R. H. 1986. Vertebrate Animals of Alabama In Need of Special Attention. Alabama Agricultural Experiment Station, Auburn University, April, 1986.

Oaks, F. L. 1989. State Preservation Officer, Alabama Historical Commission, Montgomery. Letter to Rose Weaver dated April 25, 1989.

Osborne, W. E. 1989. Geological Survey of Alabama, Geologist. Letter to Rose Weaver, February 8, 1989.

54

Raoscigno, P. 1989. U.S. Fish and Wildlife Service, National Wetlands Research Center, Slidell, Louisiana. Personal communication (504-646- 7426).

Rhinert, G. 1989. State Historical Preservation Officer. Alabama Historical Commission. Personal communication (205-261-3184).

Rosenblatt, D. H. and M. J. Small. 1981. Preliminary Pollutant Limit Values for Human Health Effects. Environ. Sei. and Technol. 14:778-783.

USATHAMA. 1978. Installation Assessment of Alabama Army Ammunition Plant, Report No. 130, May, 1978.

USEPA. 1986. Superfund Public Health Evaluation Manual. U.S. Environ- mental Protection Agency, Office of Emergency and Renedial Response. EPA/540/1-86/060 (NTIS PB87-183125).

USEPA. 1988a. Public Health Risk Evaluation Database (PHRED). U.S. Environmental Protection Agency, Office of Solid Waste and Emergency Response, Toxics Integration Branch. September 1988.

USEPA. 1988b. Integrated Risk Information System (IRIS). Office of Health and Environmental Assessment. U.S. Environmental Protection Agency. EPA/600/8-86/032a.

USEPA. 1989a. Drinking Water Health Advisory for Trinitrotoluene. Office of Drinking Water. U.S. Environmental Protection Agency (January).

USEPA. 1989b. Interim Final Guidance for Soil Ingestion Rates. J. Winston Porter, Assistant Administrator, U.S. Environmental Protection Agency. OSWER Directive 9850.4 (January 27, 1989).

Vondrick, Joseph. 1989. Laboratory Coordinator for Alabama Army Ammuni- tion Plant. Environmental Science and Engineering, Inc., Gainesville, Florida. Personal communication, March 14, 1989 (904-332-3318)

Weston Services, Inc. 1987. Alabama Army Ammunition Plant Remedial Action Operations. Final Report. Contract No. DAAA15-86-D-0014. (Area A RI only).

Weston Services, Inc. 1988. Alabama Army Ammunition Plant Area A Remedial Actions. Final Report. Contract No. DAAA15-86-D-0014. (Febru- ary).

Wright, J. 1989. Alabama Department of Economic Affairs, Montgomery, Alabama. Personal communication (205-284-8700).

55

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A-2

WORKSHEET 3-2 SCORING FOR INDICATOR SELECTION: TOXICITY INFORMATION

CHEMNAME SITE: ala TOX CLASS WT ST

Anthracene Benz(a)anthracene Benzo(a)pyrene

Bis(2-Ethylhexyl)phthalate (DEHP) Cadmium and compounds Chloroform

Chromium III and compounds Chromium VI and compounds Chrysene Copper and compounds Dibutyl phthalate Dichloromethane Diethylphtha late Dimethyl phthalate 1,3-Dinitrobenzene 2, 4-Dinitrophenol 2,4-Dinitrotoluene

2,6-Dinitrotoluene N,N-Diphenylamine Ethyl benzene Fluoranthene Iron and compounds Lead and compounds (inorganic) Mercury and compounds (inorganic) Naphthalene Nickel and compounds

Nitrate Ni trobenzene N-Nitrosodiphenylamine Polychlorinated biphenyls (PCBs)

Pyrene Trinitrotoluene (TNT) Zinc and compounds

* PC PC NC PC NC PC NC * * * NC NC NC NC * NC NC PC NC NC NC NC *

5.81E-01 4.55E+00 2.68E-02 5.71E-04 3.59E+01 5.63E-02 4.43E-02

2 2 1 2 1 2 2

.91E-05

.28E-04

.34E-06

.B6E-08

.79E-03

.81E-06

.21E-06

7.14E-01 3.81E-02 9.20E-04 2.67E-04

3 1 4 1

.57E-05

.90E-06

.60E-08

. 34E-08

4.43E+00 1.14E+00 1.09E-01 3.03E-01 3.03E-01 2.35E-02 1.10E-02

2 5 5 1 1 1 5

22E-04 71E-05 46E-06 51E-05 51E-05 17E-06 52E-07

* NC NC * PC NC * * * PC NC *

8.93E-01 1.84E+01

4 9.

46E-05 21E-04

2.29E-01 4.26E+00

1. 2.

15E-05 13E-04

1.44E+00 9.33E+01

7. 4.

20E-05 67E-03

* NC 1.07E-01 5. 33E-06

A-3

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A-5

usathama 1 - dticchemicals and supporting data is presented in table 1. the mixture of 2,4- and...

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