' . Ar'30'2397 Geraghty & Miller

Site Model November 23 1994 t Revision No. 02 5.0 NATURE AND EXTENT

The purpose of this section is to present information collected regarding the nature and extent of constituents detected at the BVL Site. The following sections present / information regarding:

1) the source of constituents; 2) the constituents detected and their nature; and, 3) the fate and transport of constituents;

The nature and extent of constituents characterized are discussed in this section and organized by medium in the following sequence: Leachate; Subsurface Soil; Upgradient Groundwater; On-Site Groundwater; Domestic Groundwater; Surface Soil; Sedimentation Basin Water and Sediment; Drainage Ditch Water and Sediment; Surface Water; Stream Sediments; Marsh Sediments; and Ambient Air. Tables 5-1 through 5-32 present summaries of the RI analytical data in the order of the text discussion. The complete validated RI data spreadsheets are provided in Volume 4 of 5, RI Analytical Data.

5.1 SOURCE OF CONSTITUENTS

The BVL is comprised of solid waste that has been exposed to precipitation and as a result, leachate has developed. The process of leachate generation at the BVL is dependent on a number of factors; however, precipitation events play a major role. Precipitation reaching the landfill surface can either evaporate, transpire, infiltrate through the landfill surface, or become surface runoff. When a sufficient amount of water infiltrates the landfill and comes into contact with the waste, leachate generation occurs. The volume of leachate generated and migrating from the landfill depends on such factors as landfill surface conditions, volume of water percolation through the cells, refuse conditions and t 5-1 ' . AR'30'2397 GERAGHTY & MILLER. INC. Site Model November 23 1994 Revision No. 02 underlying soil conditions. The relatively permeable surface and subsurface textures observed across the BVL during the field investigations suggest that precipitation can infiltrate and leachate can migrate through the soils at the surface and beneath the landfill cell; however, ponding of leachate within the cell could also occur.

Leachate generation occurs as the various waste constituents are decomposed or stabilized by aerobic and anaerobic microorganisms and converted to gases and soli e organic and inorganic compounds. The initial leaching includes the dissolution of soli material in the landfill such as salts and organic material. These dissolved constitue:.^ usually impart a brown/black color to the leachate. Biological activity within the cells will initially produce more soluble end products such as simple organic acids and alcohols. These products may undergo further biochemical reactions to release gaseous end products (e.g., carbon dioxide and methane); however, some of the soluble organic material may be leached out of the cell. In addition, organic nitrogen is converted to ammonium ions which are readily soluble and can give rise to significant quantities of ammonia in the leachate.

Initially, biological degradation of a landfill is aerobic; bu th the depletion of oxygen by microbes, anaerobic conditions quickly dominate. Therefore, a young landfill cell will contain a high concentration of organic acids, ammonia and total dissolved solids. As the landfill becomes anaerobic, a chemically reducing environment is produced which induces oxidized ions such as ferric salts to be reduced to ferrous iron and thus iron becomes soluble and leaches from the landfill cell. The temperature within a mature landfill cell is typically in the range 30 to 50° C (Crawford and Smith, 1985).

The quality of leachate from most landfills is highly variable and depends on the waste composition, depth of fill, type of cover mat --ial, operation of the landfill site, climate, and hydrogeology of the site. Various descriptio of leachates are given in the literature 5-2 $ fiR3Q2398 GERAGHTY

52 CONSTITUENT CHARACTERIZATION BY MEDIA

This section presents a discussion on the constituents detected hi leachate, subsurface soil, upgradient groundwater, on-site groundwater, domestic groundwater, surface soils, sedimentation basin water and sediment, drainage ditch water and.sediment, surface water, stream sediments, marsh sediments, and ambient air. A summary of the constituents detected for each of the media sampled is presented as Table 5-29. Where appropriate, summary data tables and figures are presented for each of the media hi the following sections. Comprehensive data tables are presented as Volume 4 of 5 of this RI Report, titled RI Analytical Data.

/ 5.2.1 Leachate

Six leachate samples (LI through L6) were collected in March 1993 from locations across the BVL (Figure 2-2). A summary of constituents detected in leachate samples is presented in Table 5-1 and illustrated on Figure 5-1.

The leachate samples contained detectable levels of toluene, 1,4-dichlorobenzene, 1,2- dichlorobenzene, 4-methylphenol, 2,4-dimethylphenol, naphthalene, 2-methyhiaphthalene, diethylphthalate at concentrations ranging from 2 ug/L to 9 ug/L. Based on the lowest observed effect levels (LOELs), these organics are typically not considered toxic to aquatic life until the levels are in the milligram per liter range. The laboratory results from the leachate samples were compared to available criteria (Table 5-1). However, the leachate seeps do not represent a habitat suitable for aquatic life. Therefore, the comparison to' t 5-3 AR302399 GERAGHTY &_ MILLER. INC. Site Model November 23 1994 Revision No. 02 criteria is for informational purposes and does not imply that an aquatic community (which is absent from the seeps) is adversely impacted. Gamma-BHC and Heptachlor were detected at 0.004 ug/L and 0.056 ug/L, respectively, in leachate sample L2. The level of heptachlor (0.056 ug/L) exceeded the USEPA criteria of 0.0038 ug/L.

Numerous inorganic constituents were detected in the leachate samples including Aluminum, barium, cadmium, calcium, chromium, cobalt, copper, iron, lead, magnesium, manganese, mercury, nickel, potassium, silver, sodium, vanadium, and zinc. The levels of aluminum, cadmium, chromium, copper, iron, lead, mercury, nickel, silver, and zinc exceed available criteria.

522. Subsurface Soil

Eight subsurface soil samples (GM2LSS, GM2LSD, GM3, GM4LSS, GM4LSD, GM5, GM6, and GM8) were collected from various depth intervals, ranging from 7 to 40 ft below ground surface, in June and July 1992. Four upgradient samples were collected: two in the storage yard M1US, GM1LSS), one across Bush Road (GM-9), and one across Bynum Run Creek (GM-7) (Figure 2-2). A summary of constituents detected in subsurface soil samples is presented in Table 5-2 and illustrated on Figure 5-2.

Ten organics were detected in on-site subsurface soil samples including: acetone, benzene, 2-butanone, carbon disulfide, 1,1-dichloroethane, methylene chloride, toluene, trichloroethene, di-n-butylphthalate, and Aroclor-1254. Total VOCs ranged from non-detect (at 6 of 12 locations) to 576 ppb at GM2LSD (Figure 5-2). Aroclor-1254 was detected at nine locations in concentration ranging from 19 ppb to 250 ppb.

5-4 t Site Model November 23 1994 Revision No. 02 Twenty-two inorganics were detected in subsurface samples including: Aluminum; Arsenic; Barium; Beryllium; Boron; Cadmium; Calcium; Chromium; Cobalt; Copper; Iron; Lead; Magnesium; Manganese; Mercury; Nickel; Potassium; Silver; Sodium; Tin; Vanadium; and, Zinc.

5.23 Groundwater

The following discussion focuses on maximum constituents concentrations detected in groundwater samples collected among the three sampling events performed in August, 1992, October, 1992 and March, 1993. Groundwater samples have been grouped for discussion purposes into upgradient, on-site (downgradient) and domestic samples. It should be noted that conjlitiifflnlsj^re^dejgcted-aijupgradient sampling locations which suggests thajLsjonia. of the upgradient sampling locations may not represent "clean background" samples.

Total and dissolved inorganic analyses were collected for ground-water samples. In most cases, dissolved inorganic constituent concentrations were lower than total inorganic constituents; however, there were exceptions. The following discussion is specific to dissolved organic constituents (except for the domestic wells where total inorganics are presented). Total inorganic constituent concentrations are also presented in the summary tables.

A summary of constituents detected is presented in Tables 5-3, 5-4, 5-5, 5-6 and 5-7 and is illustrated on Figures 5-3 and 5-4. The summary tables present frequency of detects, range of detects and maximum contaminant levels (MCLs). The MCLs presented are Maryland MCLs (Code of Maryland Regulations [COMAR], 1991). For those constituents not having Maryland MCLs, the Federal Safe Drinking Water Act MCLs (USEPA, 1992a) t 5-5 ^021*0 GERAGHTY c* MILLER Site Model November 23 1994 Revision No. 02 f are presented. Several of the constituents detected do not have state or federal MCLs. Comprehensive data tables are presented as Volume 4 of 5, titled, RI Analytical Data.

5.23.1 Upgradient Groundwater Samples

A total of four upgradient ground-water samples were collected from the upper and lower water-bearing sand zones at the BVL Site and include sampling locations GM1US, GM1LSS, GM7 and GM9. The upper sand zone is a perched sand layer, and the lower sand zone is considered the uppermost continuous water-bearing unit. Section 3.7, titled, Surface-Water and Sediment Investigations, provides a detailed discussion on the upgradient nature of these sampling locations. Groundwater samples were collected from each of the upgradient groundwater monitoring wells in August and October, 1992. A summary of constituents detected is presented,-as Table 5-3 and illustrated as Figures 5-3 and 5-4.

Eight organics were detected in upgradient groundwater samples including benzene, bromomethane, 1,1-dichloroethane, tetrachloroethene, toluene, 1,1,1-trichloroethane, trichloroethene and alpha-BHC (Table 5-3). Total VOC concentrations in upgradient samples ranged from < 10 ug/L at GM7 to 41 ug/L at GM1-US (Figure 5-3). Sample GM1- LSS and GM9 had total VOC concentrations of 5 ug/L and 7 ug/L, respectively. The total VOC results suggest that the upgradient sampling locations have been affected by the BVL or because of their upgradient nature, potentially another source.

Thirteen dissolved inorganics were detected in upgradient groundwater samples including: aluminum, barium, beryllium, calcium, cobalt, iron, magnesium, manganese, mercury, nickel, potassium, sodium and zinc. Select inorganic constituent concentrations are presented on Figure 5-4. Iron and Manganese constituent concentrations exceeded secondary MCL's for several samples. The dissolved nickel concentrations detected in 5-6 f

GERAGHTY c* MILLER. INC. Site Model November 23 1994 f Revision No. 02 GM1-US ( 0.719 and 0.846 mg/L) and GM1-LSS ( 0.275 and 0.262 mg/L) for each of the two sampling events exceeded the federal MCL of 0.1 mg/L (Table 5-3). None of the other upgradient wells or on-site or domestic well samples had nickel concentrations exceeding the federal MCL. Because these sampling locations are hydraulically upgradient from the BVL and none of the other upgradient or downgradient samples reported relatively high nickel concentrations, the source of the nickel is uncertain.

5.23.2 On-Site Giroundwater Samples

Seven on-sil:e ground-water samples were collected from the lower water-bearing sand zone at the BVL Site and include sampling locations GM2LSS, GM2LSD, GM3, GM4LSS, GM4LSD, GM5, and GM6. The lower sand zone is considered the uppermost continuous water-bearing unit and is described in detail in Section 4.0, titled, Physical Characteristics of Site. Groundwater samples were collected from each of the on-site groundwater monitoring wells in August and October, 1992. Groundwater samples were also collected from monitoring wells GM2-LSS, GM3 and GM4-LSS in March, 1993. A summary of constituents detected is presented as Table 5-4 and illustrated as Figures 5-3 and 5-4.

X Twelve organic constituents were detected in on-site or downgradient samples including: benzene, chlorobenzene, chloroethane, 1,4-dichlorobenzene, 1,1-dichloroethane, 1,2-dichloroethane, 1,2-dichloroethene (total), 1,2-dichloropropane, tetrachloroethane, trichloroethene, vinyl chloride and alpha-BHC (Table 5-4). Benzene, 1,2-dichloroethane, 1,2-dichloropropane, tetrachloroethane, trichloroethene and vinyl chloride were detected in concentrations exceeding MCLs (Table 5-4). Maximum concentrations detected for most of the twelve organic constituents detected exceeded maximum concentrations detected at upgradient sampling locations. t 5-7

GER AGHTY ? -\TTLLER IN'C Site Model November 23 1994 Revision No. 02 Total VOC concentrations in on-site samples ranged from non-detect (< 10 ug/L) at GM4-LSD to 306 ug/L at GM2-LSS. The total VOC concentration at GM2-LSS (which is only 5 feet downgradient of waste placement) was 306 ug/L. The total VOC concentration of 150 ug/L at GM3 (which is approximately 175 feet downgradient of waste placement) indicates that the level of VOCs decreases significantly with distance from the landfill. The total VOC concentrations were significantly lower at the other downgradient locations with 30 ug/L detected at GM4-LSS (which is approximately 50 feet downgradient of waste placement) being the next highest total VOC concentration. The deep lower sand samples collected from GM2-LSD and GM4-LSD were both non-detect (< 10 ug/L) indicating that VOCs are not migrating downward for any significant distance.

Fourteen dissolved inorganic constituents were detected in on-site groundwater samples including: aluminum, arsenic, barium, beryllium, calcium, cobalt, copper, iron, magnesium, manganese, nickel, potassium, sodium and, zinc. Maximum dissolved inorganic constituent concentration detected for iron (105 mg/L) exceeded the secondary MCL of 03 mg/L. Maximum dissolved inorganic constituent concentration detected for manganese (935 mg/L) exceeded the MCL goal of 02 mg/L, respectively. No other dissolved inorganic constituent concentrations exceeded available standards. Maximum dissolved inorganic constituent concentrations for arsenic, barium, beryllium, copper, iron, manganese and potassium exceeded maximum dissolved inorganic constituent concentrations from upgradient sampling locations.

5.23.3 Domestic Groundwater Samples

Ground-water samples were collected in August and October, 1992 from the three domestic wells (Milton, Fleet and Washington) adjacent to the BVL (Figure 2-2). The

5-8

GERAGHTY P STILLER. INC. Site Model November 23 1994 Revision No. 02 following paragraphs discuss separately the constituents detected in each of the three domestic wells sampled.

The Fleet domestic well is located approximately 150-feet south of the BVL in a lateral hydraulic gradient position. No organic constituents were detected in the Fleet well. Eleven inorganic constituents were detected in the Fleet well including: barium, calcium, copper, iron, magnesium, manganese, mercury, nickel, potassium, sodium, and zinc (Table 5-5). None of the constituent concentrations detected in the Fleet well exceeded MCL's. None of the constituent concentration detected in the Fleet well exceeded upgradient constituent concentrations except for Mercury during one of the two sampling events. Mercury was detected in the Fleet well during the October, 1992 sampling event at 0.00034 mg/L but was not detected at < 0.0002 for the August, 1992 sampling event. Mercury was also not detected in any of the on-site groundwater samples during the October sampling event. As a result, the detection of mercury in the Fleet well is suspect.

The Milton domestic well is located approximately 300 feet south of the BVL in a lateral hydraulic gradient position. No organic constituents were detected in the Milton well. Twelve inorganic constituents were detected including: barium, calcium, cobalt, copper, iron, magnesium, manganese, mercury, nickel, potassium, sodium and zinc (Table 5-6). None of the constituent concentrations detected in the Milton well exceeded MCL's. None of the constituent concentration detected in the Milton well exceeded upgradient constituent concentrations except for Mercury during one of the two sampling events. Mercury was detected in the Milton well during the October, 1992 sampling event at 0.00034 mg/L but was non-detect at < 0.0002 for the August, 1992 sampling event. Mercury was also not detected in any of the on-site groundwater samples during the October sampling event. As a result, the detection of mercury in the Milton well is suspect.

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GERAGHTY

5.2.4 Surface Soil

Six (6) surface soil samples (SUS4 to SUSS) were collected from 0 to 0.5 feet below ground surface at the BVL Site in August 1992 (Figure 2-2). Upgradient surface soil samples (SUS1, SUS2 and SUS3) were collected from borings located across Bynum Run flip Creek and Bush Road (Figure 2-2). A summary of the constituents detected is presented as Table 5-8 and illustrated on Figure 5-5.

The only VOC detected was Acetone in the replicate for SUS7. Bis(2- ethylhexyl)phthalate, benzo(b)fluoranthene, di-n-butylphthalate, fluoranthene, and pyrene were detected in surface soil samples at concentrations ranging from 0.054 mg/kg to 6.1 mg/kg. Of these constituents, bis(2-ethylhexyl)phthalate was detected at the highest concentration. However, this phthalate is a common laboratory contaminant, is ubiquitous in the environment, and therefore, may not be site-related.

Thirteen inorganic constituents including: aluminum, barium, beryllium, calcium, chromium, cobalt, copper, iron, manganese, mercury, nickel, sodium and vanadium were 5-10 I

GERAGHTY

Constituents were detected in surface soil sampling locations SUS-2 and SUS-3 which suggest they could be impacted by runoff from the Bush Valley Landfill (Hoover, 1993). It is unlikely that runoff from the landfill could impact these locations. The two sampling sites are 115 to 150 feet from the landfill and are on the north (opposite) bank of Bynum Run Creek which is approximately 5 feet above the normal water levels of the stream. It is possible, though unlikely, that during high flow in Bynum Run Creek water might flood the northwestern edge of the landfill. Site-related chemical constituents might then be transported as suspended sediment to sampling locations SUS-2 and SUS-3. The downstream transport (to the east) of constituents during high flow would be more * significant than any northward migration across the rapidly flowing Bynum Run Creek.

To evaluate this hypothesized pathway, the levels of inorganic constitutes at sampling locations SUS-2 and SUS-3 were compared statistically to the levels at sampling location SUS-1. The Q-test was used to make this statistical comparison (Dixon, 1951; Dean and Dixon, 1951). The test: was developed to reject outliers in small (3 to 40 samples) data sets. The constituent concentrations at sampling locations SUS-2 and SUS-3 were compared statistically to the concentrations at location SUS-1. If locations SUS-2 and SUS-3 were different, then levels of constituents at sampling location SUS-2 would be statistically less than locations SUS-2 and SUS-3 and appear as outliers. An alternate expression of these results for potential off-site differences would be to have concentrations appear statistically higher in the samples from location SUS-2 and SUS-3. The concentrations of only manganese and potassium were statistically higher at sampling locations SUS-2 and SUS-3

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GERAGHTY

The variation in manganese and potassium levels could simply be a manifestation of the two different soil types sampled (i.e., Delanco silt loam at sampling location SUS-1 vs. Codorus silt loam at sampling locations SUS-2 and 3). The inorganics observed at sampling locations SUS-1, 2, and 3 were generally within the typical range for native soils (Dragun, 1988). The sample from SUS-1 contained four constituents at levels below the typical range for soil. Manganese, potassium, sodium, and barium were less than the typical lower limit for native soils. The observed levels for these four inorganics in sample SUS-1 and the •• typical lower limit for soils were: manganese, 96 vs. 100 mg/kg; potassium, 241 vs. 400 mg/kg; sodium, 79.1 vs. 750 mg/kg; and barium 38.2 vs. 100 mg/kg. Based on this comparison to typical levels, the Delanco silt loam could be considered deficient in some inorganics rather than the Codorus silt loam containing elevated levels.

5JL5 Sedimentation Basin Water and i

A summary of constituent concentrations detected in Sedimentation Basin Water samples SW8 and SW9 is presented as Table 5-9 and Figure 5-6. Carbon disulfide was detected at SW9 at 0.032 mg/L. The samples collected from the two basins contained levels of 11 total inorganic constituents above those observed in the background samples. With the exception of aluminum, iron and lead none of the levels exceeded the available criteria.

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AR302I408 GERAGHTY & MILLER. INC. Site Model November 23 1994 Revision No. 02 The maximum total concentration for aluminum, iron and lead (2.35,3.75 and 0.0035 mg/L) exceeds the available criteria; however, the maximum dissolved levels for each of these constituents (0.0847, 0.114, and < 0.002 mg/L) is less than the available criteria. Therefore, it is unlikely that adverse ecological impacts will occur when water is present in the basins.

Each of the sedimentation basins represent depositional environments for the following reasons. The TOC levels of 30,000 and 11,OOOU mg/kg (Table 5-18) are significantly higher than the two background sites, SD1 and SD5. The basin sediments were also classified as silt and silt loam textures. Because the physical characteristics of the sediment samples from the basins are different from background samples SD-1 and 5, a direct comparison of constituent concentrations to background levels is not appropriate. The concentration of inorganics in the sedimentation basin sediment samples (Table 5-10) are generally higher than those observed in Bynum Run Creek, Bush River Tributary, and James Run sediment samples (Table 5-19 and 5-20) which is typical for fine-grained, organic-rich material. None of the constituent concentrations detected in the sedimentation basin sediment samples were greater than the NOAA ER-L (Table 5-10).

5.2.6 Drainage Ditch Water and Sediment

Organic constituents were not detected in drainage ditch water sample SW2. Sample SW2 (Figure 2-2), collected from the drainage ditch contained, levels of 11 total inorganics above those observed in 'the background samples (Table 5-11 and Figure 5-6). With the exception of aluminum, iron, and lead none of these levels exceeded the available criteria. The total concentration for aluminum, iron and lead (0.232,1.43 and 0.0082 mg/L) exceeds the available criteria; however, the dissolved levels for each of these constituents (0.0376, 0.489, and < 0.002 mg/L) is less than the available criteria. The contribution of these inorganics to Bynum Run Creek is negligible. As discussed, in Section 5.2.7, Surface Water,

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GERAGHTY & MILLER. I? Site Model November 23 1994 Revision No. 02 the levels of inorganics in Bynum Run Creek downstream from the drainage ditch, (at sampling location SW3) are not elevated above background nor do they exceed avail le criteria.

The sample from the drainage ditch represents a depositional environment. The TOC level of 33,000 mg/kg (Table 5-18) is significantly higher than the two background sites SD1 and SD5. Sediment sample SD2 was also classified as a silt loam. Because the physical characteristics of the sediment from this location is different from background samples SD1 and 5, a direct compart i to background levels is rut appropriate. Organic constituents were not detected in drainage ditch sediment sample SD2. The concentration of inorganics in this sample were generally higher than those observed in Bynum Run Creek, Bush River Tributary, and James Run (Table 5-19 and 5-20) which is typical for fine- grained, organic-rich material. None of the drainage ditch sediment constituent concentrations detected were greater than the NOAA ER-L.

52.7 Surface Water

Four surface-water samples (SW3, SW4, SW6, and SW7) were collected in August and October, 1992 from locations within Bynum Run Creek, the Bush River Tributary and the Unnamed Tributary(Figure 2-2). Two background samples (SW1 and SW5) were also collected upstream of the BVL in Bynum Run Creek and James Run (Figure 2-2). «

Results for indicator parameters are presented in Table 5-13 and Table 5-14. Results for indicator parameters appear to be similar between the first and second sampling events. Dissolved oxygen ranged from 3,0 mg/L at SW7 to 13 mg/L at SW3. Alkalinity ranged from 42 mg/L at SW4 to 90 mg/L at SW7. Biological oxygen demand (BOD) was less than 2.2 mg/L across the BVL Site. Chemical oxygen demand (COD) ranged from less than 5.0 5-14 I AR302MO GERAGHTY & MILLER. INC. Site Model November 23 1994 Revision No. 02 mg/L to 69 mg/L at SW5 which is the background sampling location in James Run. Hardness, total dissolved solids and total suspended solids were found at similar concentrations across the BVL Site. Total organic carbon ranged from 1.8 mg/L at SW4 to 7.3 mg/L at SW7. Turbidity ranged from 0.9 NTU's at SW6 to 55 NTU's at SW7. Salinity was measured at 0.0-percent at SW7.

Water-quality criteria are developed by the Maryland Department of the Environment to protect various uses of surface waters in Maryland. The segment of Bynum Run Creek adjacent to the BVL is designated as Use III, recreational trout water (COMAR, 1991). To evaluate the potential impact to Bynum Run Creek and James Run, the levels of inorganic constituents at sampling locations SW-3, SW-4 and SW-6 were compared to the concentrations observed at the two upstream control (background) sites (i.e., sampling locations SW-1 and SW-5) (Figure 2-2). Bioavailability and toxicity of inorganics to aquatic organisms vary with the form of the inorganic. Inorganics adsorbed to particulate or complexed with dissolved organic matter generally have less bioavailability than dissolved inorganics. Ambient waters, as opposed to the laboratory setting, generally contain greater inorganic binding particulate matter and dissolved organic matter. Therefore, when used for ambient waters, measurements of total recoverable inorganics (unfiltered) overestimates the ambient toxicity of inorganics that, under natural conditions, interact with particulate matter or dissolved organic matter. The Maryland regulations indicate that inorganics shall be measured as either dissolved (acid soluble) or total recoverable inorganic concentrations for comparison to the criteria (COMAR, 1991). Total recoverable inorganic concentrations cannot always be accurately equated to toxic impacts in ambient waters due to the prevalence of complexing agents that can render some inorganics nontoxic (Hall and Raider, 1993) and toxicity testing has indicated that dissolved measurements are better predictors of toxicity than total recoverable measurements (USEPA, 1992c). Therefore, concentrations of dissolved, inorganics were also compared to Maryland and USEPA criteria.

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GERAGHTY P MILLER. I^R 302^ Site Model November 23 1994 Revision No. 02 Surface-water constituent concentrations for samples collected in Bynum Run Creek, the Bush River Tributary and the Unnamed Tributary are presented in Table 5-15,5-16 and 5-17. No organics were detected in any of the surface-water samples collected from Bynum Run Creek, the Bush River Tributary or the Unnamed Tributary.

For the two samples collected from Bynum Run Creek (SW3 and SW4), the levels of inorganic constituents were generally below those observed at the upstream locations. The only exceptions were levels of dissolved mercury (SW4) total zinc and dissolved iron in the October 16, 1993 sample, and total and dissolved manganese and dissolved iron in the August 8,1993 samples. The dissolved mercury level was 0.00034 mg/L which exceeded the < 0.0002 mg/L recorded at both background sites. In addition, none of the other surface water samples contained detectable dissolved or total mercury. This result from location SW4 appears to be an anomaly. If mercury was detected at 0.00034 mg/L in the dissolved phase, it should be recorded in the total portion. Mercury was not detected (< 0.0002 mg/L) in the total portion of the 'sample. Also the detected mercury is relatively close to the detection limit and the laboratory results tend to be less accurate in this range. Considering these two concerns with the analytical data, the mercury result of 0.00034 mg/L is probably not representative of conditions in Bynum Run Creek. The maximum concentration of zinc, manganese and iron from sampling location SW4 was 0.0265 mg/L, 0.0048 mg/L and 0.156 mg/L (dissolved) respectively, which exceeds the maximum background level of 0.0156 mg/L, 0.0474 mg/L and 0.0904 mg/L (Table 5-15, Figure 5-6). The concentration of dissolved zinc in the sample was <2 ug/L. Despite exceeding the background levels, the total zinc, manganese and dissolved manganese and iron concentrations observed at sampling locations SW3 and SW4 did not exceed the available criteria. Accordingly, the zinc, manganese and iron detected in samples SW3 and SW4 does not represent an adverse impact to Bynum Run Creek.

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H^'c' MILLER. INC. Site Model November 23 1994 Revision No. 02 • The maximum average concentration of iron (total 0.428 mg/L and dissolved 0.256 mg/L) and manganese (total 0.081 mg/L and dissolved 0.079 mg/L) and magnesium (8.21 mg/L) in the samples from the Bush River Tributary (SW6) were higher than maximum levels observed in the background samples (Table 5-16, Figure 5-6). The inorganic concentrations did not exceed available criteria and these inorganics are not considered deleterious to aquatic life at these concentrations.

The samples collected from the unnamed tributary (i.e., location SW7) contained levels of 7 inorganics above those observed in the background samples (Table 5-17, Figure 5-6). However, considering the depostional nature of sampling location SW 7 compared to the background sampling locations (See section 5.2.10, titled Stream Sediment) a direct comparison of constituent concentrations is inappropriate. With the exception of total and dissolved iron, and total aluminum none of the levels of inorganics in the unnamed tributary surface water samples exceeded the available criteria. The average concentration of iron 4 (total 9.3 mg/L and dissolved 5.6 mg/L) exceeded the USEPA criteria of 1.0 mg/L and the average concentration of aluminum 0.23 mg/L exceeded the USEPA criteria of 0.087 mg/L. Because of the reducing conditions typically present in the marsh sediments, unimpacted surface water draining wetlands usually contains high iron and aluminum levels (Mitsch and Gosselink, 1986). Based on the results presented above, adverse ecological impacts are unlikely.

5.2.8 Stream Sediment

Four stream sediment samples (SD3, SD4, SD6, and, SD7) were collected from the same locations as the surface-water samples in August 1992 (Figure 2-2). Two upgradient stream sediment samples (SD1 and SD5) were collected upstream of the BVL in Bynum Run Creek and James Run. Results for indicator and physical parameters are presented

5-17 AR302U3 OERAGFTY ^ \TTLLER. INC.. Site Model November 23 1994 Revision No. 02 in Table 5-18. A summary of stream sediment constituents is presented in Table 5-19 and Table 5-20 and illustrated on Figures 5-7.

There are no established state or federal sediment quality criteria (SQC) for the protection of aquatic life, although interim SQC have been presented for several nonpolar hydrophobic organic compounds (USEPA, 1988). National Oceanic and Atmospheric Administration (NOAA) effects-based sediment quality values are available for evaluating the potential for constituents in sediment to cause adverse biological effects (NOAA, 1990). These values are not standards or criteria but are available values that can be used for comparison purposes. NOAA Effects Range Low (ER-L) and Effects Range-Median (ER- M) values were used for comparison with the detected levels of constituents in the stream sediment and marsh sediments. ER-L values are concentrations equivalent to the lower 10 percentile of available data screened by NOAA and indicate the low end of the range of concentrations at which adverse biological effects were observed or predicted in sensitive species and/or sensitive life stages. ER-M values are concentrations based on the NOAA screened data at which effects were observed or predicted in 50 percent of the test organisms evaluated. The major problem with the ER-L and ER-M is that the concentration at which toxicity was observed could not be extrapolated readily from one sediment location to another; other factors interact and influence toxicity. Sediment characteristics such as total organic carbon content can influence the contaminant toxicity; therefore, the ER-L and ER-M cannot be used as a direct indicator of adverse effects to aquatic organisms.

Only one organic constituent, 1,2-Dichloropropane at 3 ug/kg, was detected in stream sediment sample SD5 which is an upgradient background location in James Run (Figure 2- 2).

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T\'C Site Model November 23 1994 Revision No. 02 To evaluate potential impacts to streams, the levels of inorganic constituents at sampling locations SD3, SD4, and SD6 were compared to the concentrations at the two upgradient background sites (i.e., sampling locations SD1 and SD5). Most of the total organic carbon data (Table 5-18) was flagged with a "U" due to dilution effects however, the sediment samples from SD1, SD5, SD3, SD4 and SD6 contained relatively low TOC levels which ranged from 410U mg/kg at sampling location SD-3 to 1,500U mg/kg at sampling location SD-5 (Table 5-18). The sediment samples contained relatively coarse-grained material: The median (50 percent finer) size of the material ranged from 02 mm at sampling location SD-2 (described as fine sand using terminology of the American Geophysical Union, Subcommittee on Sediment Terminology [Gottschalk, 1964]) to 0.6 mm at sampling location SD1, SD3 and SD6 (coarse sand).

The concentration of inorganics in the sediment samples from Bynum Run Creek downstream from the landfill were generally less than background (Table 5-19, Figure 5-7). The levels of six inorganics (aluminum, barium, calcium, cobalt, manganese, and potassium) and cyanide in the sample from Bush River Tributary (i.e., SD6) exceeded the background concentrations (Table 5-20). However, using the Q-test, the inorganics were not statistically above background and the NOAA has not published values for these five constituents. Cyanide was observed at 2.8 mg/kg at sampling location SD6, but the maximum background level was <0.62 mg/kg. It is unlikely that concentrations of these constituents would adversely impact the aquatic community. Approximately half of the volume of the Bush River Tributary is contributed by James Run.

The sample from the Unnamed Tributary (SD7) represents a depositional environment. A comparison of SD7 results to background sample (SD1 and SD5) results was made using a Q-test (Dixon, 1951; Dean and Dixon, 1951). The Q-test was developed to reject outliers in small (3 to 40 samples) data sets. Using the Q-test the TOC level was

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I R GERAGHTY & MILLER. IN^ '' ~ " *• ^ ' Q Site Model November 23 1994 Revision No. 02 significantly (i.e., statistically) higher (29,OOOU mg/kg) than the two background sites. The sediment sample was also fine-grained composed of fine silt. Because the physical characteristics of the sediment from this location was different from background samples SD1 and SD5, a direct comparison to background levels is not appropriate. The concentration of inorganics in this sample was generally higher than those observed in Bynum Run Creek, Bush River Tributary, and James River (Table 5-19 and 5-20) which is typical for fine-grained, organic-rich material. With the exception of one inorganic, all of these levels were less than the NOAA ER-L. The sample from location SD7 contained 39.7 mg/kg of lead which incrementally exceeded the NOAA ER-L of 35 mg/kg. The difference between the measured concentrations and the NOAA values is less than the measured laboratory error for the sediment samples (i.e., RPD of 42 percent for lead based on samples SD3 and SD3/REP). Therefore, the lead in this sample could actually be less than the ER-L and definitely not pose a threat to the aquatic community.

5.2.9 Marsh Sedirqent

Nine marsh sediment samples (MSD1 through MSD9) were collected in August 1992 from the BDNRMA adjacent to the BVL. The BVL is at the headwaters of the adjacent freshwater tidal marsh; therefore, background marsh sediment sampling locations were not available within the BVL Site. Indicator and physical parameter results are presented in Table 5-21. A summary of marsh sediment constituent concentrations is presented in Table 5-22 and Figure 5-8.

The marsh sediments contained relatively high TOC levels ranging from 14,000 mg/kg at MSD6 to 28,000 mg/kg at MSD8 (Table 5-21). Grain size analysis indicates that the silt size fraction dominates the marsh sediment samples with most textures falling within

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AR302U6 GERAGHTY & MILLER. INC. Site Model November 23 1994 t Revision No. 02 the silt loam textural class. The physical data indicates that the marsh samples represent depositional areas. t

A total of nineteen inorganics were detected in marsh sediment samples including: aluminum; arsenic; barium; beryllium; calcium; chromium; cobalt; copper; cyanide; iron; lead; magnesium; manganese; mercury; nickel; potassium; sodium; vanadium; and zinc. The concentration of inorganics in the marsh sediment samples were generally higher than those observed in the stream sediments. With the exception of two inorganics, all of the levels were less than the NOAA ER-L. The sample from location MSD-1 contained 37.6 mg/kg of lead which incrementally exceeded the NOAA ER-L of 35 mg/kg (See the discussion in Section 5.2.10 titled, Stream Sediments, regarding the use NOAA ER-L values). The samples from MSD9 .contained 0.19 mg/kg of mercury which incrementally exceeded the NOAA-ER-L of 0.15. The difference between these values and their respective NOAA ER- L's is less than the measured laboratory error for the marsh sediments. Therefore, the lead and mercury in these samples could actually be less than the ER-L and definitely not pose a threat to the aquatic community.

Discharge from the two sedimentation basins, through culverts, to the marsh could be a potential pathway for the transport of site-related constituents. As a result, this potential pathway was evaluated. The concentration of constituents in the surface water and sediment from the two basins did not exceed criteria (Sections 5.2.5). The only exceptions were the levels of total aluminum, iron and lead in the surface water samples. The dissolved aluminum, iron and lead levels were less than the available criteria. Sample MSD4 was collected near the outfall from the Northeast Basin and sample MSD7 was "collected near the outfall from the Southeast Basin. Inorganic constituents at these two locations were not elevated and did not exceed the NOAA ER-L (Table 5-22). Surface water and sediment samples from the two basins demonstrate that site-related constituents

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GERAGHTY & MILLER. INC. ^ " ^ ^ ^ ^ ' ' Site Model November 23 1994 Revision' No. 02 t have not accumulated in these two areas in elevated concentrations. The two marsh sediment samples show that constituents at elevated concentrations are not transported from the sedimentation basins and deposited into the adjacent marsh.

The marsh sediment samples were collected within approximately 50 to 100 feet of the landfill. The absence of elevated inorganics at locations MSD4 and MSD7, near the basin outflows, indicates that surface water draining the landfill does not transport constituents to the adjacent marsh. The average upward hydraulic gradient (0.064 ft/ft) in monitoring wells GM-4-LSS and GM-4-LSD near the eastern edge of the landfill indicates that groundwater is discharging to the marsh and that the potential for groundwater to transport constituents significant distances away from the landfill is low. If the vertical groundwater flow was downward, more substantial off-site transport of constituents might occur.

Despite the lack of a reasonably probable pathway for constituent migration, the levels of inorganics near the landfill and some distance from the landfill were evaluated. The levels of inorganics at location MSD8 (approximately 100 feet from the landfill) served as the basis for comparing levels of inorganics in samples collected more distant from the landfill. The evaluation of the analytical data collected from the marsh show the concentrations of inorganics generally decrease with increasing distance from the landfill. A comparison of constituent concentrations detected in marsh sediment sample MSD8, which is adjacent to the landfill, to concentrations detected in samples from two distant locations is presented in Table 5-30. The concentration of inorganics was evaluated in sample MSD9 which is approximately 190 feet southeast of sample MSD8. The levels were also compared to those in sample SD7 which is approximately 210 feet northeast of sample MSD8. The concentrations for 11 of 20 constituents detected at sample location MSD9 were lower than those detected at sample location MSD8. The concentration for 8 of 19

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GERAGHTY e MILLER. INC. Site Model November 23 1994 t Revision No. 02 constituents detected at sample location SD7 were lower than those observed at sample location MSD9. As one moves farther from the landfill, constituents concentrations should continue to decrease. Therefore, based on the two isolated NOAA ER-L exceedences and the decreasing concentrations of inorganics with increasing distance from the landfill, it is unlikely that the landfill is adversely impacting the freshwater tidal and non-tidal marsh.

Organics .detected in Marsh Sediment samples included 1,2-dichloropropane, bis(2- ethylhexyl)phthalate, benzo(b)fluoranthene, butylbenzyiphthalate, di-n-butylphthalate, ------k fluoranthene, and pyrene at concentrations ranging from 0.004 to 0.72 mg/kg (Table 5-22).

The detection limits for selected organic constituents were higher than the low-range contract required detection limits (CRDLs) for soils. The occurrence of elevated detection limits for sediment samples is not uncommon. Sediment high in TOC can be a difficult matrix for the laboratory to analyze. The USEPA indicated that deleterious levels of organics could be present in the marsh sediment samples at concentrations below the elevated detection limits. To evaluate this proposed scenario, the elevated detection limits were compared to the recently published sediment quality criteria (SQC) (USEPA, 199 Ib, b, c, d, and e). The USEPA recently published SQC for two pesticides (dieldrin and eldrin) and three polynuclear aromatics (PNAs) (acenaphthene, fluoranthene, and phenanthrene). The SQC are based on the TOC present in the sample and the concentration of the specific organic constituent. The SQC are expressed as a ratio of organic constituent level (in micrograms) to TOC (in grams). The highest detection levels for these five constituents were reported for marsh sediment sample MSD8. The TOC-nonnalized levels of the two pesticides were 0.12 ug/g and the f OC-normaUzed levels of the three PNAs were 46 ug/g. The SQC for the pesticides range from 4 to 9 ug/g and the SQC for the PNAs range from 120 to 1,020 ug/g.

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•AR302M9 GERAGHTY P MILLER. INC. Site Model November 23 1994 Revision No. 02 t To further evaluate this relationship, the elevated detection limits for the pesticides and PNAs in the sample with the lowest TOC were compared to the SQC. Marsh sediment sample MSD7 continued 3,100 mg/kg of TOC. However, when the pesticide and PNA levels were normalized to TOC, the levels were again less than the SQC. Therefore, if these organics were present at or just below the detection limit in samples with high detection limits or low TOC levels, they would not cause an adverse ecological impact.

The comparison of maximum constituent concentrations detected in samples collected from the tidally influenced marsh with potentially phytotoxic soils and plant tissue concentrations derived from the literature (Kabata-Pendias and Pendias, 1992; Phytotox database, 1991) is presented in Table 5-31. Phytotoxicity is a complex interplay of constituent concentrations, soil/sediment chemistry, soil/sediment physical properties, and the physiology of the plant species involved. Subsequently, the use of generalized lists of potentially phytotoxic concentrations in soil should be reviewed with caution, when used to assess levels in marsh sediments. The maximum detected concentrations of iron in marsh sediments exceeded the potentially phytotoxic soil concentration reported in the literature (Table 5-31). The maximum concentrations of manganese, vanadium, and zinc detected in marsh sediment were within the range of potentially phytotoxic soil concentrations (Table 5-31). However, the calculated constituent concentrations of manganese, vanadium, and zinc in plant tissue did not exceed potentially phytotoxic tissue concentrations reported in the literature (Table 5-31). Evidence of plant stress indicators (i.e., spotting, discoloration of leaves and stems, chlorosis, stunted growth, abrupt changes in vegetation composition, etc.) were not observed in the marsh. Therefore, it is likely that the constituents do not have a phytotoxic effect on vegetative species in the marsh.

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GERAGHTY & VrfLd5fcU!*CH £ U C' Site Model November 23 1994 Revision No. 02 5.2.10 Ambient Air

A three-phase ambient air quality monitoring program was performed April 16,1992, September 16, 1992, and December 16, 1992, at the BVL. The ambient air sampling program was implemented to preliminarily assess the nature and extent of potential site- related volatile organic compounds (VOCs). During each sampling event one upwind sampling location was established and two downwind sampling locations were established at locations illustrated on Figure 3-3. Field data sheets from the ambient sampling programs on April 16, 1992, September 16, 1992, and December 16, 1992, are presented in Appendix G.

A summary of VOCs detected in upwind and downwind sample locations is presented as Tables 5-23 and 5-24, respectively. A comparison summary of maximum upwind and maximum downwind sampling locations is presented as Table 5-25.

Thirteen different VOCs were detected at upwind sampling locations hi concentrations ranging from 0.124 ug/m3 to 106 ug/m3 (Table 5-23). The highest VOC concentration detected at an upwind location was for methylene chloride at 106 ug/m3. Thirteen different VOCs were detected at downwind sampling locations in concentrations ranging from 0.764 ug/m3 to 240 ug/m3 (Table 5-24). The highest VOC concentration detected at an downwind location was for methylene chloride at 240 ug/m3.

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GERAGHTY & MILLER. V$$( 3 0 2 4 2 j Site Model November 23 1994 Revision No. 02 concentrations. Concentrations detected exceeded the MAAL's for Methylene Chloride, Trichloroethylene and Benzene at both upwind and downwind locations, and Carbon Tetrachloride at downwind locations.

The results indicate that constituent concentrations detected for upwind and downwind sampling were similar in that generally the same, constituents detected in downwind sampling locations were also detected at upwind sampling locations. Some constituents are present at upwind sampling locations at concentrations exceeding the downwind sampling locations. The upwind sampling results for the first sampling event should be used with the knowledge that the sampling station was placed just within the boundary of solid waste placement. However, even without the results of the first upwind sampling station, the summary and interpretation of the data would remain the same.

The detection of thirteen VOC's in the upwind sampling locations suggests that extent of ambient air contamination is not fully understood at the BVL. In addition, because the upwind station sampling results are similar to the downwind sampling results, the BVL cannot be identified as the sole source of VOC's detected in the ambient air.

53 FATE AND TRANSPORT

An evaluation of the environmental fate and transport of site-related constituents present at the BVL is important in determining the potential miaration at the site and in assessing the potential for exposure to the constituents. The ration of constituents released in the past and in the future from the site are influenced by: (1) waste characteristics; (2) site environmental characteristics; and, (3) the physical and chemical properties of the identified constituents. The waste characteristics and site environmental characteristics have been addressed in previous sections of the report. The physical and

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AR3021422 GERAGHTY & MILLER. INC. Site Model November 23 1994 Revision No. 02 chemical characteristics of the identified constituents are addressed below. The site environmental factors and physical and chemical properties are then combined to identify mechanisms of migration.

53.1 Physical, And Chemical Properties

The environmental fate and transport of constituents are dependent on the physical and chemical properties of the constituents, the environmental transformation processes affecting them, and the media through which they are migrating. Physical and chemical properties of the organic constituents identified are summarized in Table 5-32.

The water solubility of a substance is a critical property affecting environmental fate. Highly soluble constituents are generally mobile in ground and surface water. Solubilities range from less than 1 mg/L to totally miscible with most common organic chemicals falling between 1 mg/L and 1,000,000 mg/L (Lyman et al., 1990). The higher the value of the solubility, the greater the tendency of a constituent to dissolve'in water. The ketones (acetone and 2-butanone) are the most soluble of the VOCs since acetone is miscible with water and 2-butanone is only slightly less soluble. The other VOCs are less soluble than the ketones, but more soluble than the semi-VOCs. The PAHs (benzo[b]fluoranthene, fluorene, and pyrene) and Aroclor 1254 (a PCB) are the least soluble organic constituents. For inorganic constituents, solubility depends on the form of the constituent.

Volatilization of a constituent from environmental media will depend on its vapor pressure, water solubility, and diffusion coefficient. Highly water soluble compounds generally have lower volatilization rates from water unless they also have high vapor pressures. Vapor pressure, a relative measure of the volatility of chemicals in their pure state, ranges from about 0.001 to 760 millimeters of mercury (mm Hg) for liquids, with

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GERAGHTY * MILLER. INC. Site Model November 23 1994 Revision No. 02 solids ranging down to less than 10"10 mm Hg. Of the organic constituents, the VOCs have vapor pressures much greater (at least six orders of magnitude) than the semi-VOCs or PCBs.

The Henry's Law Constant, combining vapor pressure with solubility and molecular weight, is used for estimating releases from water to air. Compounds with Henry's Law Constants in the range of 10"3 atmospheres-cubic meter per mole (atm-nf/moi) and larger can be expected to readily volatilize from water (i.e., VOCs except the ketones); those with values ranging from 10"3 to 10"5 atm-nf/mol are associated with possibly significant, but not facile, volatilization (i.e., ketones and several PAHs), while compounds with values less than 10"5 atm-m3/mol will only slowly volatilize from water to a limited extent (i.e., phthalates and PAHs [except fluoranthene]) (Howard, 1989; Lyman et al., 1990). Aroclor 1254 has a relatively high Henry's Law Constant (23 x 10~3 atm-rrrVmol); however, it may not volatilize from water since it may preferentially partition to soil or sediments.

The octanol-water partition coefficient (K^) often is used to estimate the extent to which a constituent will partition from water into lipophilic parts of organisms, for example, animal fat. Similarly, the organic carbon partition coefficient (K,^) reflects the propensity of a compound to adsorb to the organic matter found in the soil or sediments. The bioconcentration factor (BCF) is the ratio of the concentration of the constituent in fish tissue to its concentration in water. As groups of compounds, the semi-VOCs and PCBs have larger K^s, K^s, and BCFs indicating a greater tendency to partition in a medium other than water.

The potential for a constituent to adsorb to soil and sediment particles will affect migration through soil and aquifer materials as well as migration from surface water to sediments. The adsorption potential typically is expressed in terms of a partition coefficient,

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GERAGHTYP MILL Site Model November 23 1994 Revision No. 02 Ky. This partition coefficient is the ratio of the concentration of adsorbed constituent to the concentration of water phase constituent. Higher values of Ky indicate a greater potential for the constituent to adsorb to soil, sediments, and aquifer materials. The partition coefficient may be determined empirically or may be estimated using constituent-specific and soil or sediment-specific parameters. The parameters most often used to calculate Ky for organic constituents are the K^ and the fraction of organic carbon (f^) in soil or sediments. The Ky for organic constituents is expressed as the product of the K^ and f^ (USEPA, 1989a). Values of Ky for inorganic constituents typically are based on several different types of leaching studies or element-specific parameters.

The inorganic constituents can be found as positively (i.e., cations) or negatively (i.e., anions) charged ions in environmental media at the BVL Site. Most of the inorganics present at the BVL, Site are found as cations and will tend to adsorb to soil materials or form insoluble precipitates, especially under neutral or basic conditions. In the soil, inorganics tend to adsorb to soil particles and can be released or desorbed from soil with changing conditions such as oxidation-reduction potential or pH. Rain water typically is mildly acidic, and the potential exists for these constituents to be leached to ground water. With the exception of cyanide (as hydrogen cyanide) and mercury in the elemental form, the inorganics are riot volatile. These two constituents most likely are not present in these forms at the site.

The constituents can be classified into categories according to their similarity in chemical, structure and/or physical and chemical properties. Both are factors influencing mobility in the environment. The constituent categories and the constituents in each category are listed below:

o Chlorinated aliphatic hydrocarbons (CAHs): carbon tetrachloride, chloroethane; chloroform; chloromethane; 1,1-dichloroethane; 1,2-

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AR3Q21425 GERAGHTY & MILLER. INC. Site Model November 23 1994 Revision No. 02 dichloroethane; 1,1-dichloroethene; 1,2-dichloroethene; 1,2-dichloropropane; meth'ylene chloride; tetrachloroethane; trichloroethene; trichlorofluoromethane; vinyl chloride. Monocyclic aromatics: benzene; bromobenzene; chlorobenzene; 1,4- dichlorobenzene; 1,2 dichlorobenzene; ethylbenzene; styrene; toluene; xylenes. Ketones: acetone, 2-butanone. Sulfides: carbon disulfide.

Phthalates: bis(2-ethylhexyl)phthalate, butylbenzylphthalate, di-n- butylphthalate; diethylphthalate. PAHs: benzo(b)fluoranthene, fluoranthene, pyrene, 4-methyphenol, 2,4- dimethyphenol, naphthalene, 2-methylnaphthalene. PCBs: Aroclor 1254. Pesticides: alpha-BHC, gamma-BHC, heptachlor Inorganics: aluminum, arsenic, barium, beryllium, boron, cadmium, chromium, cobalt, copper, cyanide, iron, lead, manganese, mercury, nickel, silver, tin, vanadium, zinc.

53.2 K*fechftnism«; Qf Migration

There are several mechanisms by which constituents may migrate through environmental media at the BVL Site. The solid waste trenches within the landfill can act as a source of constituents to other environmental media. Migration into the air can occur via volatilization or fugitive dust emissions; migration into surface water can occur through surface runoff or ground-water discharge; and migration into ground water can occur by percolation of infiltrating rain water. Potential mechanisms of migration are discussed in this section together with a discussion of constituent persistence and transformations that may occur in the source or transport medium.

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AR3Q21426 GERAGHTY p MILLER. INC. V Site Model November 23 1994 Revision No. 02 There are two processes controlling migration of constituents into air. Organic •\ - constituents may volatilize and migrate into the air and constituents adsorbed to surface soil may migrate into the air through the generation of dust either through wind erosion or mechanical means. However, the potential for fugitive dust generation at the BVL Site is considered low due to the nearly continuous vegetative covering on the landfill.

Volatilization is the mass transfer of an organic compound from a specific medium (i.e., soil) to the air. The ability for this transfer or migration to occur will depend on the other competing processes which should hinder this migration. For example, if a constituent is adsorbed strongly to soil particles, it will be less likely to volatilize into the air. Environmental factors that affect volatilization include temperature, soil porosity, soil water content, soil organic carbon content, and depth of contamination (Jury et al, 1983).

Generally, organic constituents with high vapor pressures (greater than. 10 mm Hg) or high Henry's Law Constants (greater than 10"3 atm-nf/mol) are expected to volatilize readily from soil and water. The chlorinated aliphatics, monocyclic aromatics, and fluoranthene have these properties. Aroclor 1254 also is expected to have lesser, but still substantial tendencies to volatilize; although Aroclor 1254 has a relatively high Henry's Law Constant, other processes such as adsorption influence volatility. The other organic constituents detected at the BVL Site (phthalates, benzo[b]fluoranthene, and pyrene) have lower vapor pressures than the chlorinated aliphatics and monocyclic aromatics, as well as lower water solubilities, with the net result being that volatilization can occur, although other processes may be more important in controlling their ultimate migration into air. The ketones have high water solubilities and slightly lower vapor pressures, therefore reducing the likelihood of volatilization.

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GERAGHTY & MILLER. INC. Site Model November 23 1994 Revision No. 02 Fugitive dust emissions from wind or vehicle disturbances currently are expected to be limited due to the high degree of vegetation that covers the landfill. However, the potential exists for the site to be redeveloped in the future. In the event that the vegetation is removed during construction activities, fugitive dust emissions could occur.

The environmental factors that influence wind erosion are wind speed, moisture content of soil, vegetative cover, and soil composition. Factors affecting vehicle-related emissions include soil composition and moisture content, vehicle design (e.g., weight and number of wheels), and speed of travel. Chemical and physical properties also can be used to estimate a constituent's potential to be emitted in dust. Constituents with relatively low organic carbon partition coefficients (K^. values less than 1,000) and moderate to high water solubility (greater than 1 mg/L) are more likely to be associated with the water or vapor phases than remain in soil and therefore, are unlikely to be emitted in dust. Constituents in this category are the chlorinated aliphatics, monocyclic aromatics, and ketones. The PAHs and phthalates have a moderate potential for being present in fugitive dust emissions based on these chemical properties. The PCBs have low water solubilities and high K^s, resulting in a high potential to be emitted in fugitive dust. The only PCB (Aroclor 1254) detected occurred in deep soil samples collected at depths greater than 10 to 25 feet bis and is not expected to be present in dust emanating from the soil even if construction occurred.

The inorganic constituents can either form insoluble precipitates with compounds found in soils or adsorb to soil particles. These processes result in these constituents persisting in soils, thus increasing their potential to be present in fugitive dust emissions. The migration of cyanide into air is strongly dependent on its form in soil. If cyanide is present as hydrogen cyanide, it will readily volatilize from soils. If cyanide is present complexed to a metal such as iron, it will not volatilize from soil but could be present in fugitive dust emissions-from the site. Elemental mercury is a volatile constituent. It is likely

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GERAGHTY . Site Model November 23 1994 Revision No. 02 that mercury would be present at the site as an ion, or as part of a complex, and therefore would not be volatile.

53:2.1 Migration in Soil

The more soluble constituents may migrate through soil to the shallow ground water. The more volatile constituents or those strongly adsorbed to dust may migrate into air, as discussed in the previous section. The more soluble constituents may migrate with infiltrating precipitation to the ground water. Typically, organic constituents with high water solubilities and low K^s are particularly susceptible to this phenomenon. The more mobile constituents at the BVL Site are expected to be the chlorinated aliphatics, monocyclic aromatics, and ketones. In general, the PAHs, PCBs, and phthalates are not very mobile and would not be expected to readily percolate into ground water.

The migration of inorganic chemicals from and through soil to ground water is influenced by soil characteristics and water movement. Soil parameters of importance are cation and anion exchange capacities of the soil (i.e., the interaction between positively and negatively charged ions), organic carbon content, pH, oxidation-reduction potential, and porosity. In general, positively charged inorganic constituents (cations) (i.e., most of the inorganic constituents) will be retarded by clays which exhibit an overall negative charge. Anions such as cyanide will be more mobile in such soils.

-- ' 5322 Migration in Surface Water

Surface-water runoff from the BVL either infiltrates the more permeable portions of the ground surface or is collected by the unlined ditches on the northern and southern edge of the BVL. Runoff is directed towards either the northeast or southeast

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GERAGHTY & MILLER. INC. ft K 0 U £ \ L ? Site Model November 23 1994 Revision No. 02 sedimentation basin. The ditch leading to the southeast sedimentation basin has not been maintained. As a result water directed toward the southeast sedimentation basin does not actually reach the basin and surface-water runoff drains into the adjacent property to the south and ultimately to tidal marsh. Constituents in soil and leachate with high water solubilities and low K^ values may be transported via surface runoff into surface water. Constituents with low water solubilities and high K^ values may be transported through erosional processes. These constituents bound to soil can be transported to the ditches and directed to the sedimentation basins.

During heavy rain storms, the potential exists for the sedimentation basins to be overwhelmed with runoff and overflow resulting in constituents being transported into the low-lying areas. Upon reaching the surface water, constituents may remain in the water column, volatilize, or adsorb to bottom or suspended sediments. The constituents that are likely to have a high tendency to volatilize have been described in the previous section. Constituents with low water solubilities and/or high K^s such as PAHs, PCBs, and phthalates will tend to associate with sediments.

The behavior of the inorganic constituents in surface water is affected by water- quality parameters such as pH, temperature, hardness, and dissolved oxygen. Inorganic compounds can occur in aquatic systems as dissolved ions, dissolved complexes with organic and inorganic chemicals, colloids, or particulates. The solubility and mobility of metals is enhanced by their ability to form complexes with humic and fulvic acids, carbonates, hydroxides, and phosphates. In many cases, toxicity to aquatic organisms is reduced by the presence of these complexing agents. The results of surface-water sampling indicate that the site has not significantly impacted surface water in the vicinity of the BVL. These results may be interpreted to indicate that the inorganics present in soil or ground water at

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GERAGHTY & MILLER. INC Site Model November 23 1994 Revision No. 02 the BVL are not transported to surface water possibly due to adsorption to soil or aquifer materials.

533 Biodegradation and Biotransfonnation Processes

Biological and chemical processes occurring in surface soil can be important in determining the ultimate fate of the constituents in soils at the BVL Site. The extent and rates of these reactions are difficult to predict for each individual site. Microorganisms naturally occurring in soils are able to use several organics as a food source, degrading the components ultimately to carbon dioxide and water (Kostecki and Calabrese, 1989).

Benzene, ethylbenzene, toluene, and xylenes may be degraded aerobically (i.e., in the presence of oxygen) in soils (Kostecki and Calabrese, 1989). In surfitial soils, biodegradation can be relatively rapid, provided adequate amounts of oxygen, moisture, and nutrients (e.g., nitrogen, phosphorus) are available. Aerobic metabolism of constituents under these conditions may result in the total depletion of oxygen. When this happens, the microorganisms may begin utilizing inorganic ions, such as nitrate or sulfate, and continue aerobic respiration, or other types of microorganisms may become active in metabolizing the constituent (ILSEPA, 1989a). i The PAHs adsorbed onto soil also can be biodegraded. Factors which contribute to the degree to which biodegradation occurs include biodegradability rates, production of intermediates, and the effects of mixtures. In general, PAHs with 2 or 3 rings (e.g., phenanthrene) were more readily degraded than PAHs with 4 or more rings (e.g., pyrene) (McKenna and Heath, 1976).

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GERAGHTY & MILLER. INC. Site Model November 23 1994 Revision No. 02 In most cases, an organic contaminant is not broken down completely to carbon dioxide and water by a bacterium but is metabolized to an intermediate, which is in turn further degraded. The metabolites isolated depend primarily on the time at which the reaction is stopped. In the course of the degradation of phenanthrene to low molecular weight carboxylic acids by soil Pseudomonads (bacteria), a total of 24 different metabolites have been either isolated or proposed as intermediates (Pucknat, 1981). All of these intermediates are more water soluble than the parent compound and are therefore more mobile.

The extent to which constituents may biodegrade also can be affected by their presence in mixtures. As noted above, some PAHs are more degradable than others. If both stable and mobile PAHs are present in a mixture, the more degradable materials may be co-metabolized at a rate similar to or faster than the more stable compounds.

CAHs, in general, have high aqueous solubilities and high VPs, relatively low soil sorptions as predicted by the K^s, extremely slow hydrolysis rates, and relatively rapid oxidation rates (USEPA, 1979b). CAHs are more readily biotransformed under anaerobic, reducing conditions. Under these conditions, microbially-mediated reductive dehalogenation will be a major environmental fate process. Constituents that are strongly sorbed to particles and organic matter are less available for biotransformation. In ground water, CAHs are degraded slowly by anaerobic processes. For example, isomers of 1,2- dichloroethene may be formed in ground water through the biological transformation of tetrachloroethane and trichloroethene involving anaerobic, reductive dehalogenation; the subsequent dechlorination of dichloroethene results in the formation of vinyl chloride (USEPA, 1985; Bamo-Lage et al., 1986). The detection of 1,2-dichloroethene and vinyl chloride in the samples collected at the site may be evidence of the degradation of tetrachloroethane and trichloroethene.

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GERAGHTY

5.4 EXPOSURE CHARACTERIZATION

The information collected during the RI investigations will be used by USEPA to develop an exposure characterization with regard to human health and the environment. The potential for exposure in conjunction with the analytical data will then be used by USEPA to develop the Baseline Risk Assessment. Section 4.8 titled, Ecological Assessment provides potential receptor survey and analysis of migration pathways for the ecological communities identified at the BVL Site.

5.5 SUMMARY AND CONCLUSIONS

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GERAGHTYc^ MILLER. INCAR302i433 Site Model November 23 1994 Revision No. 02 runoff. Leachate is also migrating downward through the waste and is entering the groundwater system beneath the landfill, which has affected on-site and off-site groundwater. Because groundwater discharges to the marsh and adjacent stream segments, constituents have the potential to migrate off-site via groundwater. The results indicate that landfill constituents are also migrating via the ambient air pathway. A detailed summary of the constituents detected for each of the media sampled is presented in the previous sections. Organic and inorganic constituents were detected in on-site and off-site media, which is typical for an unlined municipal landfill. In addition, the number and concentration of constituents detected in each of the media sampled decreases with distance from the site, which is also typical for a municipal landfill.

An evaluation of the fate, transport and extent of site-related constituents detected in various media at the BVL Site was performed. The results indicate that there are limits to the extent of constituents detected that are attributable to the BVL and that there is not widespread gross contamination of the off-site media that represents an imminent hazard to human health or the environment. Groundwater, leachate and on-site surface soils represent the media most affected by the landfill; although leachate seeps are a result of the landfill operation, as opposed to an affected media.

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r;cp AOUTV z, NfTLLER. [NIC ^,* • Site Model November 23 1994 Revision No. 02 indicate that constituent concentrations detected in surface water samples collected from the marsh and stream segments are much lower than groundwater concentrations, indicating that natural attenuation is contributing significantly to the reduction of landfill constituent concentrations with distance from the landfill.

On-site leachate seeps and on-site surface soils represent a source of landfill constituents that are available to migrate off-site via surface water runoff to the adjacent marsh area and streams. The results indicate that constituent concentrations detected hi off- site media are much lower than constituent concentrations detected in on-site media, indicating that natural attenuation is contributing significantly to the reduction of landfill constituent concentrations with distance from the landfill.

The information collected during the RI investigations regarding the nature and extent of landfill constituents has been used by USEPA to develop an exposure characterization with regard to human health and the environment. The potential for exposure in conjunction with the analytical data has also been used by USEPA to develop the Baseline Risk Assessment, referenced as Volume 5 of 5, which discusses the actual and potential risks associated with the constituent concentrations detected.

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,?• ^TILLER IN'C Prelim. I.D. of ARARs November 23, 1994 Revision No. 02 6.0 PRELIMINARY IDENTIFICATIQN OF ARARS

The primary concern during the development of remedial action alternatives for hazardous waste sites under the Comprehensive Environmental Response, Compensation, and Liability Act (CERCLA) is the degree of human health and environmental protection afforded by a given remedial action. The National Oil and Hazardous Substances Contingency Plan (NCP), as amended pursuant to the Superfund Amendments and Reauthorization Act (SARA), requires that primary consideration be given to remedial alternatives which make CERCLA response actions consistent with other pertinent Federal and State environmental requirements. Under SARA, remedial actions must address any applicable or relevant and appropriate requirements (ARARs) under other Federal laws, and any more stringent State standards or requirements. Refer to the EPA document "CERCLA Compliance With Other Laws Manual," dated August 8,1988 (OSWER Directive 9234.1-01), for a list of potential ARARs for specific remedial technologies that could be considered during the FS process.

Currently, EPA CERCLA guidance calls for a preliminary identification of potential ARARs as part of the RI to assist in initial identification and screening of remedial alternatives. Because of the interactive nature of the RI/FS process, ARAR identification continues through the RI/FS as better understanding is gained of site conditions, site contaminants, and potential remedial alternatives. The following ARARs have been identified at this stage of the project and may be categorized as chemical-specific, location- specific, and action-specific. It should be recognized that the following list of ARARs is preliminary and that ARARs identified herein will be evaluated during the Feasibility Study (FS). It is therefore likely that some of the ARARs will drop out of the analysis and others could be added.

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AR302I436 GER AGHTY » VTTLLER. INC. Prelim. I.D. of ARARs November 23, 1994 Revision No. 02 6.1 CHEMICAL-SPECIFIC ARARSs

Chemical-specific ARARs are usually health- or risk-based numerical values or methodologies which, when applied to site-specific conditions, result in the establishment of numerical standards. These standards establish the acceptable concentration of a chemical that may be found in, or discharged to, the ambient environment. If a chemical has more than one such requirement (ARARs), the most stringent generally should be complied with. Refer to Table 6-1 for a list of potential chemical-specific ARARs that have been identified for the BVL Site.

62 LOCATION-SPECIFIC ARARSs .

A site's location is a fundamental determinant of its impact on human health and the environment. Location-specific ARARs are restrictions placed on the concentration of hazardous substances or the conduct of activities solely because they are in specific locations. Some examples of special locations include floodplains, wetlands, rivers, or sensitive ecosystems or habitats. Refer to the EPA document "CERCLA Compliance With other Laws manual," dated August 8, 1988 (OSWER Directive 9234.1-01), for more details. Refer to Table 6-1 for a list of potential location-specific ARARs that have been identified for the BVL Site.

63 ACnON-SPEOFIC 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 actions that are selected to accomplish a remedy. Since there are usually several alternative actions for any remedial site, very different

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Q n o i Q "7 GERAGHTY & STILLER. Iv"" Prelim. I.D. of ARARs November 23, 1994 Revision No. 02 requirements can come into play. These action-specific requirements do not in themselves determine the remedial alternative; rather, they indicate how a selected alternative must be achieved. Refer to Table 6-1 for a list of potential action-specific ARARs identified for the BVL Site.

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GERAGHTY < Findings And Conclusions November 23, 1994 Revision No. 02 7.0 FINDINGS AND CONCLUSIONS

7.1 SUMMARY

Remedial Investigation field work performed at the BVL has focused on several major objectives. These objectives are to:

• Define the nature and extent of ground water, soil, surface water, sediment and air contamination resulting from the Bush Valley Landfill; • Define the interaction of the ground water and surface water regimes; Evaluate the presence and quality of leachate emanating from the landfill; and, Develop sufficient environmental data to support the evaluation of remedial alternatives as part of the Feasibility Study.

The field work conducted between the months of February 1992 and March 1993 included the following major, tasks:

Surface Geophysical Survey - A surface magnetometer survey was conducted across the BVL, to provide information on the distribution of buried metal within the cells to identify the existence of areas, if any, where buried drums may occur. Ambient Air Monitoring - Three separate air monitoring events were conducted to preliminarily characterize the nature and magnitude of releases from the BVL to the air media across the site. For each sampling event, three stations were established to collect low volume samples over a four-hour time duration.

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GERAGHTY p MILLER. I\TC Findings And Conclusions November 23, 1994, Revision No. 02 Monitor Well Installation - A total of 12 monitor wells were installed around the periphery of the landfill cells to evaluate subsurface geologic conditions, localized ground water flow conditions, and to ascertain the chemical quality of ground water emanating from the landfill. Marsh Piezometer Installation - A series of piezometers were installed along three transects extending out into the marsh east of the BVL to evaluate the hydraulic relationship of shallow ground water and the surface water regime. 'Surface Water Investigation - Surface water samples were collected from Bynum Run Creek, James Run Creek, the Bush River Tributary, the Unnamed Tributary and from other areas including sedimentation basins, the drainage ditch and observable leachate seeps to characterize the chemical quality of surface water and surface water runoff. Soil/Sediment Investigation - Surface soil, stream sediments, marsh sediments, sediments in the drainage basin and the ditch were collected at and in the vicinity of the BVL to ascertain the presence of contamination migrating from or a result of the BVL. Ecological Assessment - A field survey within the vicinity of the BVL was conducted to identify ecological and vegetative communities, to evaluate migration pathways and to preliminarily assess impacts to ecological receptors.

Based on the field tasks performed over the last two years, Geraghty & Miler has established the hydrogeologic framework within the vicinity of the Bush Valley Landfill and has characterized the various media sufficiently to permit the assessment of real and potential risk. The field tasks performed have provided the necessary environmental data to define the source and to evaluate the pathways for contaminant transport.

12 LANDFILL DESIGN AND CONSTRUCTION

Based on pre-design construction drawings prepared in 1974 by Edwin Otis Weaver (Maryland Professional Engineer #3766), the existing BVL was initially started as a "trench

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GERAGHTY <* MILLER. INC. Findings And Conclusions November 23, 1994 Revision No. 02 operation". Design drawings illustrate ten (10) trenches covering approximately 16 acres oriented east to west approximately 50-feet wide and up to 25-feet deep, separated by a five (5) foot buffer strip. Design trenches are illustrated with a bottom elevation of approximately 13 feet mean sea level and are reportedly within approximately five feet of the water table. It is believed that the above ground portion of the BVL was constructed from the south to north starting with a "buffer berm" built above ground surface along the southern property line.

Geraghty & Miller completed a magnetometer survey at the BVL on February 26, 1992. The survey was performed to provide information on the distribution of buried metal in the BVL that may help in identifying areas, if any, where buried drums occur. The magnetic response (gamma) over the BVL is characterized by a high level of noise. While the magnetometer data does provide information on the distribution of metal across the BVL, there is so much metal that is so widespread and causing such high noise, that the data is limited for isolating areas that potentially contain drums.

73 SITE-SPECIFIC GEOLOGY - i The BVL Site is underlain by two (2) distinct sand layers separated by finer textured materials. The uppermost sand layer is encountered approximately five (5) to twenty (20) feet below ground surface (15 to 25 ft. msl.) and varies in thickness from two (2) to ten (10) feet. The upper sand zone was identified at location GM1, GM2, GM9, MW2, Milton and Fleet. However, the thickness and physical characteristics vary between locations suggesting the possibility that the upper sand zone may not be continuous between locations. The upper sand zone does not exist or becomes non-distinct to the east of the BVL.

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AR302H GERAGHTY & MILLER! INC. Findings And Conclusions November 23, 1994 Revision No. 02 The upper and lower sand zones are separated by a layer of finer grained material that is variable in thickness and texture. The separation layer was observed to range from 10 to 15 feet in thickness. The fine-grained material separating the upper and lower sand zones is dominated by clay and silt and the sand fraction tends to increase with depth as the lower sand zone is approached. Shelby tube samples collected from the separation layer at locations GM1 and GM9 demonstrated a vertical permeability of 6.5 X 10"7 and 3.1 X 10~a cm/sec, respectively.

The second or lower sand zone is encountered approximately 35 feet below ground surface (5 ft. msl.) on the west side of the BVL and less than 20 feet below ground surface (3 ft. msl.) on the east side of the BVL. The upper contact of the lower sand zone appears to slope to the south-southeast. The thickness of the lower sand unit was observed to be at least 20 to 30-feet.

7.4 SITE-SPECIFIC HYDROGEOLOGY

The upper sand zone is described at location GM1, GM2, GM9, MW2, Milton and Fleet. However, the thickness and physical characteristics vary between locations suggesting the possibility that the upper sand zone may not be continuous between locations. Saturated conditions in the upper sand zone have only been observed at GM1. Therefore, it is likely that the upper sand zone is intermittently or seasonally saturated at some locations. Based on the information collected during the RI, the upper sand zone may not contribute significantly to the ground-water flow characteristics of the BVL Site.

The lower sand zone is considered the uppermost continuous water-bearing unit. Ground-water elevations collected in January and May, 1993 indicate that the primary direction of ground-water flow is from west to east across the BVL to the Tidal Marsh and

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AR302H2 GERAGHTY & MILLER. INC. Findings And Conclusions November 23, 1994 Revision No. 02 the Unnamed Tributary of the Bush River which serve as the discharge boundaries for the ground water regime. The ground-water flow rate from west to east across the site within the lower sand zone was calculated to range from 2,6 X 10~3 to 2.6 ft/day.

7.5 SURFACE-WATER HYDROLOGY

Surface-water from the northern portion of the BVL Site eventually is directed to Bynum Run Creek. Stream flow in Bynum Run Creek to the north of the BVL was measured at approximately 3,100 gpm. Bynum Run Creek converges with the southward flowing James Run, which flows into the Bush River Tributary 1000 feet northeast of the BVL. Surface-water flow in the Bush River Tributary was measured at approximately 4,300 gpm. Surface-water from the southern and eastern portion of the BVL is directed into the freshwater tidal marsh area to the east. The area east of the,BVL is drained by an Unnamed Tributary to the Bush River.

During the spring of 1992 leachate seeps were present on the west, north and east sides of the BVL. Leachate seeps were not observed from May to December, i992. Therefore, the leachafe seeps at the BVL were observed to flow only during "wet" months of the year between January and April. The leachate seeps typically originate on the sides of the BVL, but more towards the upper portions. Leachate water from the seeps along the west side of the BVL either infiltrates to the subsurface or migrates towards the southern drainage ditch. Leachate water from seeps along the north side of the BVL either infiltrates to the subsurface or migrates toward the northeast sedimentation basin. Leachate water from the seeps along the east side of the BVL either infiltrates to the subsurface or migrates towards the sedimentation basins. Typical flow associated with the leachate seeps across the BVL is minimal; the leachate seeps appear to produce water in the range of 0.1 to 0.5 gpm

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GERAGHTY & MILLER. INC. Findings And Conclusions November 23, 1994 Revision No. 02 (based on visual observations) during peak flow periods which are limited to "wet" months of the year.

7.6 ECOLOGICAL ASSESSMENT

Seven terrestrial communities, four wetland communities and one riverine community type were identified. Ecological and vegetative communities identified and surveyed included upland forest, floodplain forest, swamp, fresh tidal mar-~ non-tidal marsh, man- made isolated wetlands, hedgerows, fields, lawns, open areas, and the landfill. The ecological inventory performed for the BVL Site produces a species list of terrestrial flora and fauna that is both large and varied. Indications of environmental impact stress to life forms were not observed. The flora and fauna were noted to be in good condition. Rare, threatened, endangered and/or protected plant or animal species (as list the Natural Heritage Program of the Maryland DNR), were not identified. Sufficient information regarding the nature and extent of constituents detected at the site and how they potentially affect the ecological environment has been collected to support the screening of potential remedial alternatives. In addition, the data collected to date indicates that the BVL has not had an adverse impact on the ecological community and that additional work as part of a secondary ecological assessment is not needed.

7.7 MEDIA CHARACTERIZATION

7.7.1 Leachate

Six leachate samples (LI through L6) were collected in March 1993 from locations across the BVL. The leachate samples contained detectable levels (range 1 to 9 ug/L) of volatile and semi-volatile organic compounds, including toluene, dichlorobenzene(s),

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Numerous inorganic constituents were detected in the leachate samples including Aluminum, barium, cadmium, calcium, chromium, cobalt, copper, iron, lead, magnesium, manganese, mercury, nickel, potassium, sodium, vanadium, and zinc. The levels of aluminum, cadmium, chromium, copper, iron, lead, mercury, nickel, silver, and zinc exceed available criteria.

7.7.2 Subsurface Soil

Eight subsurface soil samples (GM2LSS, GM2LSD, GM3, GM4LSS, GM4LSD, GM5, GM6, and GM8) were collected from various depth intervals, ranging from 7 to 40 ft below ground surface. Several organic constituents were detected in on-site subsurface soil samples including acetone, benzene, 2-butanone, carbon disulfide, 1,1-dichloroethane, methylene chloride, toluene, trichloroethene, di-n-butylphthalate, and Aroclor-1254 (Table 5-2). Total VOCs ranged from non-detect (at 6 of 12 locations) to 576 ppb at GM2LSD (Figure 5-2). Aroclor-1254 was detected at nine locations in concentration ranging from 19 ppb to 250 ppb.

Numerous inorganic constituents were detected in subsurface samples including aluminum, arsenic, barium, beryllium, boron, cadmium, calcium, chromium, cobalt, copper,

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GERAGHTYP MILLER. Findings And Conclusions November 23, 1994 Revision No. 02 iron, lead, magnesium, manganese, mercury, nickel, potassium, silver, sodium, tin, vanadium and zinc.

7.73 Grnnndwater

7.73.1 Upgradient Groundwater Samples

A total of four upgradient ground-water samples were collected from the upper and lower water-bearing sand zones at the BVL Site. Eight organics were detected in upgradient groundwater samples including benzene, bromomethane, 1,1-dichloroethane, tetrachloroethene, toluene, 1,1,1-trichloroethane, trichloroethene and alpha-BHC (Table 5- 3). Total VOC concentrations in upgradient samples ranged from non-detect (less than 10 ug/L) to 41 ug/L. The total VOC results suggest that the upgradient sampling locations have been affected by the BVL or because of their upgradient nature, potentially another source.

Thirteen dissolved inorganics were detected in upgradient groundwater samples. Only iron and manganese constituent concentrations exceeded available criteria (i.e., secondary MCLs) for selected samples. In addition, dissolved nickel was detected in a single well cluster (GM1) at concentrations which exceed the federal MCL of 0.1 mg/1.

7.732 On-Site Groundwater Samples

Seven on-site ground-water samples were collected from the lower water-bearing sand zone at the BVL Site. Twelve organic constituents were detected hi on-site or downgradient samples including benzene, chlorobenzene, chloroethane, 1,4-dichlorobenzene, 1,1- dichloroethane, 1,2-dichloroethane, 1,2-dichloroethene (total), 1,2-dichloropropane,

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GERAGHTY & MILLER. INC. Findings And Conclusions November 23, 1994 Revision No. 02 tetrachloroethane, trichloroethene, vinyl chloride and alpha-BHC (Table 5-4). Benzene, 1,2- dichloroethane, 1,2-dichloropropane, tetrachloroethane, trichloroethene and vinyl chloride were detected in concentrations exceeding MCLs. Maximum concentrations detected for most of the twelve organic constituents detected exceeded maximum concentrations detected at upgradient sampling locations.

Total VOC concentrations in on-site samples ranged from non-detect (< 10 ug/L) at GM4-LSD to 306 ug/L at GM2-LSS. The total VOC concentration at GM2-LSS (which is only 5 feet downgradient of waste placement) was 306 ug/L. The total VOC concentration of 150 ug/L at GM3 (which is approximately 175 feet dpwngradient of waste placement) indicates that the level of VOCs decreases significantly with distance from the landfill. The total VOC concentrations were significantly lower at the other downgradient locations with 30 ug/L detected at GM4-LSS (which is approximately 50 feet downgradient of waste placement) being the next highest. The deep lower sand samples collected from GM2-LSD and GM4-LSD were both non-detect (< 10 ug/L) indicating that VOCs are not migrating downward in the lower sand zone for any significant distance.

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GERAGHTY

Ground-water samples were collected from the three domestic wells (Milton, Fleet and Washington) adjacent to the BVL. No organic constituents were detected in either sampling events from the Milton and Fleet domestic wells. Although several inorganic constituents were detected in both wells, none of the constituents exceeded MCLs or secondary standards (Table 5-5).

The Washington domestic well is located approximately 650-feet to the southwest of the BVL in an upgradient position. One organic, alpha-BHC, was detected at a concentration similar to detections in other upgradient monitor wells. Two inorganic constituents, aluminum and iron exceeded the secondary MCLs.

7.7.4 Surface Soil

Six (6) surface soil samples were collected from 0 to 0.5 feet below ground surface at locations on-site and off-site (upgradient) of the BVL. Several semi-volatile and inorganic constituents were detected in surface soil samples (Table 5-8). Constituent concentrations detected in on-site soils for chromium and mercury exceeded available standards.

Despite the detection of selected constituents in surface soils off-site from the landfill, (SUS1 and SUS2 across Bynum Run Creek) it is unlikely that the constituents detected are a result of site related surface water/sediment transport. To eliminate this pathway, off-site constituent concentrations were compared statistically (Q-test) to upgradient constituent concentrations (SUS1). The absence of significant differences for most inorganics between

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GERAGHTY & MILlfeR.&fr? 4 U 8 Findings And Conclusions November 23, 1994 Revision No. 02 the off-site and upgradient sampling locations indicates that each of the off-site upgradient sampling locations were not impacted by the BVL.

7.7.5 Sedimentation Basin Water and Sediment

The water samples collected from the two basins contained levels of 11 inorganic constituents above those observed in the background samples (Table 5-9). With the exception of total aluminum, iron and lead none of the constituent concentrations exceeded the available criteria. However, the maximum dissolved concentrations for aluminum, iron and lead is less than the available criteria. The concentration of inorganics in the basin samples were generally higher than those observed in the other surface water sediment locations which is typical given the fine-grained organic rich depositional nature of the sample. None of the constituent concentrations detected in the sedimentation basin sediment samples were greater than the NOAA ER-L values (Table 5-10). Therefore, it is unlikely that adverse ecological impacts will occur as a result of water or sediments present in the basins.

7.7.6 Drainage Ditch Water and Sediment

The water sample collected from the drainage ditch contained concentrations of 11 total inorganic constituents above those observed in the background samples (Table 5-11). With the exception of total aluminum, iron, and lead none of these levels exceeded the available criteria. However, the maximum dissolved concentrations for aluminum, iron and lead is less than the available criteria. The contribution of these inorganics to Bynum Run Creek is negligible. As discussed, in Section 5.2.7, Surface Water, the levels of inorganics in Bynurn Run Creek downstream from the drainage ditch, (at sampling location SW3) are not elevated above background. The concentration of inorganics in the drainage ditch

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AR302H9 GERAGHTY & MILLER. INC. Findings And Conclusions November 23, 1994 Revision No. 02 sample were generally higher than those observed in the other stream sediment locations which is typical given the fine-grained organic rich depositional nature of the sample. None of the drainage ditch sediment constituent concentrations detected were greater than the NOAA ER-L (Table 5-12). Therefore, it is unlikely that adverse ecological impacts will occur as a result of water or sediments present in the drainage ditch.

7.7.7 Surface Waters

Four surface-water samples were collected during two separate sampling events from locations within Bynum Run Creek, the Bush River Tributary and the Unnamed Tributary. In addition, two background samples were collected upstream of the BVL in Bynum Run Creek and James Run.

To evaluate the potential impact to Bynum Run Creek and James Run, the levels of inorganic constituents at downstream sampling locations were compared to the concentrations observed at the two upstream control (background) sites. No organics were detected in any of the surface-water samples. For the samples collected from Bynum Run Creek, and the Bush River Tributary the levels of inorganic constituents were generally below those observed at the upstream locations (Tables 5-15 and 5-16). With the exception of total aluminum, none of the constituents detected in Bynum Run Creek exceeded available criteria. Several constituent concentrations detected in the unnamed tributary were greater than constituent concentrations detected at upgradient sampling locations. However, with the exception of total and dissolved iron and total aluminum, none of the concentrations of inorganics in the unnamed tributary exceeded the available criteria (Table 5-17). Because of the reducing conditions typically present in the marsh sediments, unimpacted surface water draining wetlands usually contains high iron and aluminum levels. Therefore, no adverse impact to surface waters is attributable to the BVL

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GERAGHTY

7.7.8 Stream Sediments

Four stream sediment samples (one sampling event) were collected from the same locations as the surface-water samples. Two upgradient stream sediment samples were collected upstream of the BVL in Bynum Run Creek and James Run, The concentration of inorganics in the sediment samples from Bynum Run Creek and the Bush River Tributary were generally less than background concentrations (Table 5-19 and 5-20). The concentration of inorganics in the unnamed tributary sample were generally higher than background which is typical for fine-grained, organic rich depositional environments. With the exception of one organic, lead, (which incrementally exceeded the NOAA ER-L) detected in the unnamed tributary all of the levels were less than available criteria. Based on the analysis of stream sediments no adverse impact to stream sediments is attributable to the BVL Site.

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Nine marsh sediment samples were collected from the BDNRMA adjacent to the BVL, The marsh sediment samples were collected within approximately 50 to 100 feet of the landfill in areas of surface water/sediment deposition and groundwater discharge.

The evaluation of analytical data collected from the marsh samples shows the concentrations of inorganics generally decreases with distance from the landfill. The upward vertical hydraulic gradient (0.064 ft/ft) in monitoring wells GM-4-LSS and GM-4-LSD near the eastern edge of the landfill indicates that groundwater is discharging to the marsh and that the potential for groundwater to transport constituents significant distances away from the landfill is limited. If the vertical groundwater flow was downward, more substantial off- site transport of constituents might occur. Organic constituents, primarily semi-volatile

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GERAGHTY & MILLER. INC. Findings And Conclusions November 23, 1994 Revision No. 02 organics were detected in marsh sediments, however, constituent concentrations were judged to be below deleterious levels (Table 5-22). The absence of elevated inorganics at locations MSD4 and MSD7, near the basin outflows, indicates that surface water draining the landfill does not transport constituents to the adjacent marsh. Based on two isolated NOAA ER-L exceedences (lead at MSD1 and mercury at MSD9) and the decreasing concentrations of inorganics with increasing distance from the landfill, it is unlikely that the landfill is adversely impacting the freshwater tidal and non-tidal marsh.

7.7.10 Ambient Air

A three-phase ambient air quality monitoring program was performed April 16, 1992, September 16, 1992, and December 16, 1992, at the BVL. Thirteen different VOC constituents were detected at both upwind and downwind sampling locations at relatively low concentrations (Table 5-25). The highest VOC concentrations detected were for methylene chloride at 240 Mg/m3. The results indicate that constituent concentrations detected between upwind and downwind locations were similar in that generally the same constituents detected in downwind sampling locations were also detected at upwind sampling locations.

Constituent concentrations were compared to "Multimedia Environmental Goals" (MEGs), which may be used to set guideline concentrations for specific compounds based on human health effects. All concentration values were observed to be well below their appropriate MEG concentration (Table 5-25). Constituent concentrations were also compared to Maryland Acceptable Ambient Levels (MAAL's) for annual average concentrations. Concentrations detected exceeded the MAAL's for Methylene Chloride, Trichloroethylene and Benzene at both upwind and downwind locations, and Carbon Tetrachloride at downwind locations. Because the upwind sampling results are similar to

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GERAGHTY & MILLER. INC. Findings And Conclusions November 23, 1994 Revision No. 02 the downwind sampling results, the BVL cannot be identified as the source of VOC's detected in the ambient air.

7.8 CONCLUSION

The BVL is comprised of solid waste which in itself serves as the primary source of potential contaminants. The solid waste has been exposed to precipitation and as a result, leachate containing landfill constituents has developed and is migrating via several primary pathways. Leachate is migrating laterally within the landfill and has formed leachate seeps along the side slopes which serve as a source of landfill constituents. The leachate seeps have affected on-site soils and landfill constituents can migrate off-site via surface water runoff. Leachate is also migrating downward through the waste and is entering the groundwater system beneath the landfill, which has affected on-site and off-site groundwater. Because groundwater discharges to the marsh and adjacent stream segments, constituents have the potential to migrate off-site via groundwater. The results indicate that landfill constituents are also migrating via the ambient air pathway. A detailed summary of the constituents detected for each of the media sampled is presented in the previous sections. Organic and inorganic constituents were detected in on-site and off-site media, which is typical for an unlmed municipal landfill. In addition, the number and concentration of constituents detected in each of the media sampled decreases with distance from the site, which is also typical for a municipal landfill.

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GERAGHTY

Constituents are migrating downward through soils and entering the groundwater system as evidenced by constituents detected in on-site and off-site groundwater samples. However, comparison of constituent levels at various locations indicates that constituent concentrations decrease with distance from the landfill in the groundwater media. Lanof':U constituents detected in off-site groundwater samples are concentrated in the area south and east of the BVL. It is expected that the unnamed stream segment to the south of the BVL and the stream segment in the middle of the marsh area east of the BVL represent the lateral extent of constituents hi groundwater attributable to the BVL. The results also indicate that constituent concentrations detected in surface water samples collected from the marsh and stream segments are much lower than groundwater concentrations, indicating that natural attenuation is contributing significantly to the reduction of landfill constituent concentrations with distance from the landfill.

On-site leachate seeps and on-site surface soils represent a source of landfill constituents that are available to migrate off-site via surface water runoff to the adjacent marsh area and streams. The results-indicate that constituent concentrations detected in off- site media are much lower than constituent concentrations detected in on-site media, indicating that natural attenuation is contributing significantly to the reduction of landfill constituent concentrations with distance from the landfill.

The Remedial Investigation for the Bush Valley Landfill has provided sufficient environmental data for each of the media of concern to allow the assessment of real and potential risk by establishing the various components of the transport pathway(s) from source to receptors. The information generated through the performance of the Remedial

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AR302l*5i* GERAGHTY & MILLER. INC. Findings And Conclusions November 23, 1994 Revision No. 02 Investigation is sufficient to meet the objectives of defining the nature and extent of contamination, defining the interactions of the ground water and surface water regimes, evaluating the presence and quality of leachate emanating from the landfill, and developing necessary data to support the evaluation of remedial alternatives to be performed as part of the Feasibility Study.

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GERAGHTY & MILLER. INC. References November 23, 1994 Revision No. 02 8.0 REFERENCES SECTION 1 - INTRODUCTION Geraghty & Miller, Inc., 1992. Work Plan, Remedial Investigation/Feasibility Study, Bush Valley Landfill, Harford County, Maryland. Consultant's report prepared for the Department of Public Works, Harford County, Maryland. February. U.S. Environmental Protection Agency (USEPA), 1990. National Oil and Hazardous Substances Pollution Contingency Plan; Final Rule. Office of Emergency and Remedial Response. Washington, DC. March 8. SECTION 3 - SITE INVESTTGATTVE ACTT% £§ U.S. Environmental Protection Agency, 1991. USEPA Contract Laboratory Program, National Functional Guidelines For Organic Data Review. U.S. Environmental Protection Agency. June 1990. "Contract Laboratory Program: Statement of Work for Analysis of Ambient Air. Exhibit D, Section 1, Part IB." Research Triangle Park, North Carolina. U.S. Environmental Protection Agency, 1988a. Laboratory Data Validation Functional Guidelines For Evaluating Organic Analyses. Prepared by USEPA Data Review Work Group. U.S. Environmental Protection Agency, 1988b. Laboratory Data Validation Functional Guidelines For Evaluating Inorganic Analyses. Prepared by USEPA Data Review Work Group. U.S. Environmental Protection Agency. December 1986. "Quality Assurance Handbook for Air Pollution Measurement Systems, Volume II: Ambient Air Specific Methods." Research Triangle Park, North Carolina. EPA-600/9-72-005. NTIS PB-254 658. U.S. Environmental Protection Agency. April, 1984. "Compendium of Methods for the Determination of Toxic Organic Compounds in Ambient Air." Research Triangle Park, North Carolina EPA-600/4-84-041.

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GERAGHTY c9 MILLER. INC. W References November 23, 1994 Revision No. 02 SECTION 4 - PHYSICAL CHARACTERISTICS OF SITE Baker, W.L., 1972. Eastern Forest Insects. U.S. Dept. of Agriculture, Washington, DC. Brown, M.L. and R.G. Brown, 1984. Herbaceous Plants of Maryland. University of Maryland, College Park, MD. Brown, M.L. and R.G. Brown. 1972. Woody Plants of Maryland. University of Maryland, College Park, MD. Conant, R., 1958. A Field Guide to Reptiles and Amphibians. Houghtin Mifflin Company, Boston, MA. Gleason, HA., and A. Cronquist, 1991. Manual of Vascular Plants of Northeastern United States and Adjacent Canada. New York Botanical Garden, NY. Harford County, Department of Planning and Zoning, 1988. Harford County Land Use Plan. July, 1988 Kaston, B J., and E. Kaston, 1953. How to Know the Spiders. W.C. Brown Co., Dubuque, IA. Maryland Natural Heritage Program, 1991. Rare, Threatened, and Endangered Plants of Maryland. Department of Natural Resources, Annapolis, MD. Maryland Natural Heritage Program, 1991. Rare, Threatened, and Endangered Animals of Maryland. Department of Natural Resources, Annapolis, MD. McKegg, J., 1992. Maryland Department of Natural Resources. Letter to Michael Dant of Geraghty & Miller, Inc. July 30. NUS Corporation, Superfund Division. 1985. "Site Inspection of Bush Valley landfill." December 10, 1985. NUS Corporation, Superfund Division. 1986. "A Hazard Ranking System for Bush Valley Landfill." April 9, 1986. Paradise, J.L., 1969. Mammals of Maryland. Bureau of Sport Fisheries and Wildlife, Washington, DC.

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GERAGHTY Insect Guide. Doubleday & Co., New York, NY. Webster, W.D., J.F. Parnell, and W.C. Briggs, Jr., 1985. Mammals of the Carolinas, Virginia, and Maryland, Univ. of North Carolina, Chapel Hill, NC. White, C.P., 1989. Chesapeake Bay, A Field Guide. Tidewater Publishers, Centreville, MD. Wolfin, J.P., 1992. United States Fish and Wildlife Service, Division of Ecological Services. Letter to Michael Dant of Geraghty & Miller, Inc. July 27. SECTION 5 - NATURE AND EXTENT Agency for Toxic Substances and Disease Registry (ATSDR), 1989a. Draft Toxicological Profile for Cobalt. Public Health Services, U.S. Department of Health and Human Services, Atlanta, GA. Agency for Toxic Substances and Disease Registry (ATSDR), 1989b. Draft Toxicological Profile for Silver. Public Health Service, U.S. Department of Health and Human Services, Atlanta, GA. Agency for Toxic Substances and Disease Registry (ATSDR), 1990. Draft Toxicological t Profile for Manganese. Public Health Service, U.S. Department of Health and Human Services, Atlanta, GA. Agency for Toxic Substances and Disease Registry (ATSDR), 199 la. Draft Toxicological Profile for Bis(2-ethylhexy)phthalate. Public Health Service, U.S. Department of Health and Human Services, Atlanta, GA.

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GERAGHTY & MILLER. INC. References November 23, 1994 Revision No. 02 Agency for Toxic Substances and Disease Registry (ATSDR), 199 Ib. Draft Toxicologic Profile for Aluminum. Public Health Service, U.S. Department of Health and Human Services, Atlanta, GA. Agency for Toxic Substances and Disease Registry (ATSDR), 1991c. Draft Toxicological Profile for Barium and Compounds. Public Health Service, U.S. Department of Health and Human Services, Atlanta, GA. Agency for Toxic Substances and Disease Registry (ATSDR), 1991d. Draft Toxicological Profile for Cadmium. Public Health Service, U.S. Department of Health and Human Services, Atlanta, GA. Agency for Toxic Substances and Disease Registry (ATSDR), 199le. Draft Toxicological Profile for Selected PCBs (Aroclor 1260, 1254, 1248, 1242, 1232, 1221, and 1016). Public Health Service, U.S. Department of Health and Human Services, Atlanta, GA. Agency for Toxic Substances and Disease Registry (ATSDR), 1992a. Draft Toxicological Profile for Mercury. Public Health Service, U.S. Department of Health and Human Services, Atlanta, GA. Agency for Toxic Substances and Disease Registry (ATSDR), 1992b. Draft Toxicological Profile for Zinc. Public Health Service, U.S. Department of Health and Human Services, Atlanta, GA. Barrio-Lage, G., F.Z. Parsons, R.S. Nasser, and P.A. Lorenzo, 1986. Sequential Dehalogenator of Chlorinated Ethenes. Environ. Sci. Technol., 20:96-99. Briggs, G.C., R.H. Bromilow, and AA. Evans, 1982. Relationships Between Lipophilicity and Root Uptake and Translocation of Non-ionized Chemicals by Barely. Pesticide Science, 13:495-504. Budavari, S., (Ed.), 1989. The Merck Index. An Encyclopedia of Chemicals. Drugs, and Biolopcals. Eleventh Ed. Merck & Co., Inc., Rahway, NJ. 1606 pp. Chapman, P.M., 1989. Current Approaches to Developing Sediment Quality Criteria. Environmental Toxicology and Chemistry, 8:598-599. Code of Maryland Regulations (COMAR), 1991. Water Quality, 26.08.02, Maryland Department of the Environment. July 1.

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GERAGHTY & MILLER. INC. References November 23, 1994 Revision No. 02 Connell, AJ. and J. Miller, 1984. Ecotoxicolgy and Chemistry. Lewis Publishers, New York, NY.

Crawford, J. F., and P. G. Smith. 1985. Landfill Technology. Butterworths, Boston, MA, 157 p.

Davis, W.B, 1978. The Mammals of Texas. Texas Parks and Recreation Department, Bulletin No. 41. Dean, R.B. and WJ. Dixon. 1951. Simplified statistics for small numbers of observations. Anal. Chem., 23(4): 636-638. Di Toro, D.M., C.S. Zarba, DJ. Hansen, WJ. Berry, R.C. Swartz, C.E. Cowan, S.P. Pavlou, H.E. Alien, N.A. Thomas, and P.R. Paquin, 1991. Technical Basis for Establishing Sediment Quality Criteria for Nonionic Organic Chemical Using Equilibrium Partitioning. Environmental Ecotoxicology and Chemistry, 10:1541-1583. Dixon, WJ. 1951. Ratios involving extreme values. Ann. Math. Stat., 22: 68-78. Eisler, R., 1986. Polychlorinated Biphenyl Hazards to Fish, Wildlife, and Invertebrates: A Synoptic Review. U.S. Fish and Wildlife Service. Biological Report 85(1.7), April. 72pp. Hall, J.C. and R.L. Raider, 1993. A Reflection on Metals Criteria. Water Environment & Technology. June. Hazardous Substances Databank (HSDB), 1993. On-line Computerized Database National Library of Medicine Toxicological Data Network. Howard, P.H., 1989. Handbook of Environmental Fate and Exposure Data for Organic Chemicals. Volume I. Large Production and Priority Contaminants. Lewis Publishers, Inc., Chelsea, MI. 574 pp. Howard, P.H., 1990. Handbook of Environmental Fate and Exposure Data for Organic Chemicals. Volume H. Solvents. Lewis Publishers, Inc., Chelsea, MI. 546 pp. Howard, P.H., R.S. Boethling, W.F. Jarvis, W.M. Meylan, and E.M. Michalenko, 1991. Handbook of Environmental Degradation Rates. Lewis Publishers, Inc., Chelsea, MI. 725pp.

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GERAGHTYc* MILLER. INC. ^ 4 b U References November 23, 1994 Revision No. 02 Integrated Risk Information System (IRIS), 1993. U.S. Environmental Protection Agency, Office of Health and Environmental Assessment, Cincinnati, OH. Junor, FJ.R., 1972. Estimation of the Daily Food Intake of Piscivorous Birds. The Ostrich 43(4): 193-205. Jury, W.A., W.F. Spencer, and WJ. Fanner, 1983. Behavior Assessment Model for Trace Organics in Soil: I. Model Description. J. Environ. Qual., 12:558-564. Kabata-Pendias, A., and H. Pendias, 1992. Trace Elements in Soils and Plants. Second Edition, CRC Press. Boca Raton, FL. 365 pp. Kostecki, P.T., and EJ. Calabrese, 1989. Petroleum Contaminated Soils. Volume I. Remediation Techniques, Environmental Fate, Risk Assessment. Lewis Publishers, Inc., Chelsea, MI. 357 pp. Lugg, G.A., 1968. Diffusion Coefficients of Some Organic and Other Vapors in Air. Analytical Chemistry, 40(7): 1072-1077. Lyman, WJ., W.F. Rheel, and D.H. Rosenblatt, 1990. Handbook of Chemical Property Estimation Methods. McGraw-Hill, Inc., New York, NY. Martin, A.C., H.S. Zim, and AJL Nelson, 1951. American Wildlife and Plants: A Guide to Wildlife Food Habits. Dover Publications, Inc., New York, NY. Maryland Department of the Environment (MDE), 1991. Screening Levels for Common Toxic Air Pollutants. Air Management Administration, Baltimore, MD. January. Montgomery, J.H., and L.M. Welkom, 1990. Ground Water Chemicals Desk Reference. Lewis Publishers, Inc., Chelsea, MI. 640 pp. Moriarty, F., 1988. Ecotoxicologv: The Study of Pollutants in Ecosystems. Second Edition. Academic Press, New York, NY. McKenna, E J., and R.D. Heath, 1976. Biodegradation of Polynuclear Aromatic (soil and ground water) Hydrocarbon Pollutants by Soil and Water Microorganisms. Water Resources Center, University of Illinois, Research Report No. 113. UILV-WEC-76- 0113.

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GERAGHTY & MILLER. IN" References November 23, 1994 Revision No. 02 National Oceanic and Atmospheric Administration (NOAA), 1990. The Potential for Biological Effects of Sediment-Sorbed Contaminants Tested in the National Status and Trends Program. NOAA Tech. Memo. NOS OMA 52. Osweiler, G.D., T.L. Carson, W.B. Buck, and G.A. Van Gelder, 1985. Clinical and Diagnostic Veterinary Toxicology. Third Edition. Kendall-Hunt Publishing Company, Dubuque, Iowa. Pucknat, A.W., ed, 1981. Health Impacts of Polynuclear Aromatic Hydrocarbons. Noyes Data Corporation, Park Ridge, NJ. Shea, D., 1988. Developing National Sediment Quality Criteria. Environmental Science and Technology, 22(11): 1256-1261. Shen, TJ., 1982. Air Quality Assurance for Land Disposal of Industrial Waste. Environ. Mgmt, 6:297-305. Terres, J.K., 1991. The Audubon Society Encyclopedia of North American Birds. Wings Books, New York, NY. 1109pp. U.S. Environmental Protection Agency (USEPA), 1992a. Drinking Water Regulations and Health Advisories. Office of Solid Waste and Emergency Response, Washington, DC. April. U.S. Environmental Protection Agency (USEPA), 1992b. Health Effects Assessment Summary Tables, Annual FT-1992. Office of Solid Waste and Emergency Response, Washington, DC. U.S. Environmental Protection Agency (USEPA), 1992c. Interim Guidance on Interpretation and Implementation of Aquatic Life Criteria for Metals. Office of Science and Technology Health and Ecological Criteria Division, Washington, DC. May. U.S.Environmental Protection Agency (USEPA), 1992d. Framework for Ecological Risk Assessment. EPA 630/R-92/001. U.S.Environmental Protection Agency (USEPA), 1992e. Toxic Substances Spreadsheet. Water Quality Standards Unit. October 19.

8-7

AR302J462 GERAGHTY e MILLER. INC. References November 23, 1994 Revision No. 02 U.S. Environmental Protection Agency (USEPA), 1991. Toxic Substance Spreadsheet. Water Quality Standards Unit, Region IV. February 25. ' U.S.Environmental Protection Agency (USEPA), 199 Ib. Proposed Sediment Quality Criteriafor the Protection of Benthic Organisms: Acenaphthene, Dieldrin, Endrin, Fluorene, Phenanthrene. Office of Science and Technology, Health and Ecological Criteria Division, Washington, DC. November. U.S.Environmental Protection Agency (USEPA), 1990. Assessment of Risks from Exposure of Humans, Terrestrial and Avian Wildlife, and Aquatic Life to Dioxins and Furans from Disposal and Use of Sludge from Bleached Kraft and Sulfurin Pulp and Paper Mills. Office of Toxic Substances, Washington, DC. EPA 560/5-90/013. U.S. Environmental Protection Agency (USEPA), 1989a. Transport and Fate of Contaminants in the Subsurface. Seminar Publication, Center for Environmental Research Information, Cincinnati, OH. U.S. Environmental Protection Agency, 1989b (USEPA). Risk Assessment Guidance for Superfund, Volume 1, Human Health Evaluation Manual (Part A). Office of Emergency and Remedial Response, Washington, DC. U.S.Environmental Protection Agency (USEPA), 1989c. Briefing Report to the EPA Science Advisory Board on the Equilibrium Partitioning Approach to Generating Sediment Quality Criteria. Office of Water Regulations and Standards, Criteria and Standards Division, Washington, DC. U.S. Environmental Protection Agency (USEPA), 1988. Interim Sediment Criteria Values for Nonpolar Hydrophobic Organic Contaminants. Office of Water Regulations and Standards Division, Washington, DC. U.S. Environmental Protection Agency (USEPA), 1986. Quality Criteria for Water. Office of Water Regulations and Standards, Washington, DC. U.S. Environmental Protection Agency (USEPA), 1985. Chemical, Physical, and Biological Properties of Compounds Present at Hazardous Waste Sites. Office of Waste Programs Enforcement, Washington, DC.

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fl'R302l*63 GERAGHTY

SECTION 6 - PR^y, JMTNARY IDENTIFICATION OF ARARS U.S. Environmental Protection Agency (USEPA), 1988. CERCLA Compliance With Other Laws. Office of Emergency and Remedial Response, Washington D.C. OSWER Directive 9234.1-01. August 8.

8-9

GERAGHTY & MILLER. INC. TABLE 2-1 CHRONOLOGY OF EVENTS AT BUSH VALLEY LANDFILL

Date Description Prior to 1974 The site was used as farmland or left fallow as an open field. 1974-1975 Site begins operating as landfill, 8/25/75 DHMH permits site as RCRA Subchapter D municipal sanitary landfill Permit No. 75-12-01-02A. 1975-1978 Numerous inspection reports by DHMH and HCHD show that site not being operated in accordance with permit and state law. 10/20/78 DHMH orders Harris family to undertake specific actions to correct design and operational deficiencies to bring landfill into compliance with the permit and state law. 5/16/79 DHMH orders Harris family to correct design and operational deficiencies to bring the landfill in compliance with the permit and state law; and DHMH orders Harris family to hire Maryland Environmental Services to take charge of and to operate the Bush Valley landfill and to pay the salaries of the MES personnel sent to take charge of and operate the Bush Valley Landfill. 7/79-12/80 Maryland Environmental Services personnel take charge of and operate the Bush Valley T andfill site. 5/2/80 DHMH orders Harris brothers to correct design and operational deficiencies to bring the landfill in compliance with the permit and Maryland law. 3/3/81 DHMH order suspending 1975 permit, ordering Harris brothers to stop accepting solid waste at the landfill and ordering Harris brothers to correct design and operational deficiencies in violation of its permit and state law. 5/12/81 DHMH hearing on 3/3/81 order. 5/21/81 DHMH findings of fact and order directing Harris family to stop accepting solid waste at the landfill and to begin closure of the landfill.

^302465 GERAGHTY & MILLER. INC. TABLE 2-1 (Continued) CHRONOLOGY OF EVENTS AT BUSH VALLEY LANDFILL

Date Description 7/27/81 SC-0-82-109 violation citation 394.

3/8/82 C-0-82-151 COMAR 10/17/11/04E violations citation-permit suspended. 3/31/82 Hearing A2-E-66, if Harris family complies with 3/8/82 order (admitting violations from 1/1/82 to 3/8/82), family will not be cited for other violations.

5/11/82 DHMH order requiring Harris family to correct design and operational deficiencies and permitting Harris family to accept solid waste at the landfill until 5/31/82, at which time closure activities to commence. 9/7/82 C-0-83-047, civil penalty assessment of $5,000. Unclaimed certified letter by Harris. 12/21/82 C-0-83-047, $5,000 civil penalty order delivered to Harris family. 2/1/83 Hearing A2-E-282, DHMH assesses $1,000 penalty against Harris family. 1983 Harris family abandons landfill. 2/20/84 No response from Harris family relative to noncompliance orders. Referred to Attorney General's Office for enforcement action. 8/84 MDE concludes preliminary assessment—preliminary assessment report submitted to EPA. 12/85 EPA completes a site inspection and assigns an HRS of 40.29. 6/88 EPA places Bush Valley Landfill site on National Priorities List. 1/89 By cooperative agreement, Bush Valley Landfill is assigned to MDE as a state lead response action.

GERAGHTY & MILLER. INC.fi R 3 0 2 h 6 6 TABLE 2-1 (Continued) CHRONOLOGY OF EVENTS AT BUSH VALLEY LANDFILL

Date Description 11/89 MDE contracts with Dynamac Corporation to develop a work plan for RI/FS. 5/22/90 PRP letters issued. 6/90 County begins good faith negotiations with EPA. 10/15/90 EPA approves of Geraghty & Miller, Inc. as County's prime contractor to conduct RI/FS. 12/21/90 County and EPA execute AOC for RI/FS. 1/21/92 Harford County holds public information meeting. 2/4/92 USEPA conditionally approves Work Plan. 2/24-26/92 Geraghty & Miller performs Magnetometer Survey. 2/27/92 Harford County submits Ambient Air Monitoring Program Work Plan. 3/31/92 • USEPA verbally approves Ambient Air Monitoring Program Work Plan. 4/16/92 First Ambient Air Sampling Event performed. 6/8/92 Final access agreements acquired. 6/29/92 Drilling Program initiated. 8/3/92 First Environmental Sampling Event initiated. 9/92 Ecological Inventory field investigations performed. 10/12/92 Second Environmental Sampling Event initiated. 3/12/93 Third Environmental Sampling Event initiated.

GERAGHTY & MILLER. 1^ 3 Q 9 h fi 7 TABLE 2-1 (Continued) CHRONOLOGY OF EVENTS AT BUSH VALLEY LANDFILL '

Date Description 3/25/93 Geraghty & Miller presents preliminary results of RI to Harford County, USEPA and MDE. 5/93 Draft RI submitted to USEPA.

CHRONOEVE.TBL/BUSHVALLEVTU3-93

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V) c/l tn Q VI o Ul t/i '/I M 1 r* rt * »rt « r* » 0 - C 2 t 1 1 1 1 1 1 Tla * 1 1 1 1 i S S S cu z i r«( I N N M M N M N N M > - S S S S i i^t o C O Q O S s si C/l « 2 2 > o O o 0 'w o S < — S "S _ i « — 3 O JS TABLE 2-3 CONCENTRATIONS OF CONSTITUENTS DETECTED DURING THE 1984 SITE INSPECTION

~~Sample Concentration MCLs Location Compounds (ug/1) Ug/L)~~

Diggs Home* N-nitrosodipheny'iamine Toluene 5 2,000 Iron 357 Braxton/Harris Home Diethylhexylphthlate Aluminum 8,590 Iron 8,660 Manganese 51 Lead 13 50 Chromium 16 100 Sedimentation Basin Sediment Samples Toluene 0.050a Arsenic 9.9a 50 Aqueous Samples Iron 3,540 Aluminum 4,210 Manganese 4,210 Leachate Benzene 22 Chlorobenzene <5 Total Xylenes <5 10,000 Chloroethane 14 0.5 DEHP <10 21,000 Bynum Run Creek Downstream Silver , 10 50

~~MW-1 N-nitrosodiphenylamine 10 Bis(2-ethylhexyl)phthalate 10 Di-n-butyl-phthalate 10 Di-ethylphthalate 10 Phenanthrene 10 Methylene Chloride 5 Carbon Disulfide 1.4 Aluminum 35,200 (continued)~~

~~GERAGHTY & MILLER. Ifyft 3 Q 2 k 1 0 TABLE 2-3 (Continued) CONCENTRATIONS OF CONSTITUENTS DETECTED DURING THE 1984 SITE INSPECTION~~

~~Sampl e Location Compounds Concentration MCLs (ug/1) (ug/L)~~

MW-1 (cont.) Arsenic 44 50 Cadmium 2.4 10 Chromium (total) 809 100 Cobalt 104 Copper 553 Iron 190,000 Lead 126 50 Manganese 1,130 Mercury 0.63 2 Nickel 269 Tin 62 Vanadium 749 Zinc 668 MW-2 Bis(2-ethylhexyl)phthal ate 10 Di-n-butylphthalate 10 Aniline 5 Methyl ene chloride 5 Aluminum 25,200 Arsenic 34 50 Beryllium 6- Cadmium 1.2 10 Chromium (total) 328 100 Cobalt 96 Copper 337 Iron 319,000 Lead 164 50 Manganese 1,020 .. Nickel 195 Tin 82 Vanadium 405 Zinc 358 (continued)

~~GERAGHTY & MILLER. INCfl R 3 0 2 k 1 TABLE 2-3 (Continued) CONCENTRATIONS OF CONSTITUENTS DETECTED DURING THE 1984 SITE INSPECTION~~

~~Sample Compounds Concentration MCLs Location (ug/1) (ug/L)~~

MW-4 Phenol 10 Di-n-butylphthalate 10 01 -ethyl phthal ate 10 Aniline 95 Trans-l,2-Dichloroethe~2 10 100 Vinyl chloride 12 .Chloroethane 14 Hethylene chloride 85 1,1-Dichloroethane 65 V 1,2-Dichloroethane 22 0.5 1,1,1 -Trichl oroethane 5 1,2-Dichloropropane 15 Trichloroethene 8 Tetrachloroethene 19 5 Chlorobenzene 5 Benzene 22 Total xylenes 5 10,000 Carbon disulfide 1 Aluminum 13,100 Arsenic 75 50 Cadmium 3 10 Chromium (total) 322 100 Cobalt 96 Copper 819 Iron 367,000 Lead 53 50 Manganese 1,690 Mercury 0.46 2 Nickel 506 Tin 62 Vanadium 749 Zinc 668 a - units are mg/kg *The Diggs home is south of the Milton and Fleet homes. MCLs - Maximum contaminant levels Source: NUS, 1985, 54 FR 22062, and OSWER Directive 9355.3-03. (b) The MCL's listed are those that were in effect in 1984 No information is available to indicate whether metals results are from filtered or unfiitered samples.

~~GERAGHTY & TABLE 2-4 HISTORICAL MONITORING WELL SAMPLING RESULTS, VOLATILE ORGANIC COMPOUNDS~~

~~Concentration (ug/L) Compound MW-1 MW-2 MW-4 7/7/88 2/22/90 7/7/88 2/22/90 7/7/88 2/22/90~~

Chloromethane <1 <5 <1 <5 11 <5 Bromomethane <1 <1 <1 <1 <1 <1 Dichlorodifluoromethane <1 <1 <1 <1 6 <1 Vinyl Chloride <1 <1 <1 <1 2 <1 Chloroethane <1 <1 <1 <1 12 <1 Methylene Chloride <1 <1 <1 <1 <1 <1 Trichlorofluoromethane <1 <1 <1 <1 <1 <1 1,1-Dichloroethene <1 . <1 <1 <1 <1 <1 1,1-Dichloroethane <1 <1 21 23 <1 Trans-l,2-Dichloroethane <1 <1 <1 1 4 <1 Chloroform <1 <1 <1 <1 <1 <1 1,2-Oichloroethane <1 <1 <1 2 <1 1 • 1,1,1-Trichloroethane <1 <1 <1 <1 <1 11 Carbon Tetrachloride <1 <1 <1 <1 <1 <1 Bromodichloromethane <1 <1 <1 <1 <1 <1 1,2-Dichloropropane <1 <1 <1 <1 4 <1 Trans-l,3-Dichloropropene <1 <1 <1 <1 <1 <1 Trichloroethene <1 <1 6 <1 3 <1 Dibromochloromethane <1 <1 <1 <1 <1 4 1,1,2-Trichloroethane <1 <1 <1 <1 <1 <1 CIS-1,3-Dichloropropene <1 <1 <1 <1 <1 <10 2-Chloroethylvinylether <1 <10 <1 <10 <1 <1 Bromoform <1 <1 <1 <1 <1 <1 1,1,2,2-Tetrachloroethane <1 <1 <1. <1 <1 <1 Tetrachloroethene <1 <1 •

~~GERAGHTY & MILLER. INC. A R 3 0 2 4 7 J TABLE 2-4 (Continued) HISTORICAL MONITORING WELL SAMPLING RESULTS, VOLATILE ORGANIC COMPOUNDS~~

~~Concentration (ug/L) Compound MW-1 MW-2 MW-4 7/7/88 2/22/90 7/7/88 Z/22/90 7/7/88 2/22/90~~

~~Oichlorofluoromethane <1 Ethyl Ether 1 <1 99 Acetone NO N-Butanol Trichlorofluoroethane <1 Chlorodif1uoromethane Carbon Disulfide 101 10 Methyl-tart-butyl ether 22 Styrene 2 ND~~

Source: MDE Files: State of Maryland, Department of Health and Mental Hygiene (DHMH), Trace Organics Laboratory Results. Note: MW-3 has been dry since 1982. MW-1, MW-2, and MW-4 have been sampled for VOCs since 1983, and for heavy metals/inorganic compounds since 1976. Sampling method used is EPA Method 601. Detection limits are represented by the < symbol. ND = Non-detected where as a blank means not reported.

~~GERAGHTY & MILLER. INC4 R 3 0 2 k 1 k TABLE 2-5 HISTORICAL MONITORING WELL SAMPLING RESULTS- METALS/INORGANIC COMPOUNDS~~

~~Concentration (ug/L) Compound MW-1 MW-2 MW-4 7/16/87 8/29/89 7/7/88 8/29/89 7/7/88 8/29/89~~

Aluminuni Arsenic <10 <10 <10 <10 <10 <10 Barium < 100 < 100 <100 <100 <100 <100 Beryllium -- -- — ~ " ~ Cadmium 9 <10 <100 <10 <10 < 10 Chromium (total) < 10 < 10 <10 <10 <10 <10 Cobalt ~ - - - Copper <50 <50 80 <50 <50 <50 Iron 43,200 45,200 10,510 42,730 14,750 10,520 Lead <50 <50 <10 <50 <50 <50 Manganese 3,830 920 970 1,520 310 680 Mercury <0.5 <0.5 <0.5 <0.5 13 <05 Nickel — . ~ — — — — Selenium <10 <10 <10 <10 <10 <10 Silver -- — — " ~ "" Tin — ~~ ~~ ~™ — — Vanadium - - ~ - .. . " ~ Zinc 1,340 <100 33 <10 170 <50 Antimony — — — "" ~~ Potassium. 2,400 4,800 - 1,800 - 4,400

Source: MDE Files: State of Maryland, Department of Health and Mental Hygiene (DHMH), Trace Organics Laboratory Results. Note: MW-3 has been dry since 1982. MW-1, MW-2, and MW-4 have been sampled for VOCs since 1983, and for heavy metals/inorganic compounds since 1976. Sampling method used is EPA Method 3005/SW846 Detection limits are represented by the < symbol. Unknown whether samples were filtered prior to preservation. - Blank means data not reported.

~~HISTORIC.TBL/BUSHVALLEY-RI-3/93~~

~~GERAGHTY & MILLER. INg.fj 3 Q 2 ^ 7 5 TABLE 2-6 SUMMARY OF MONITORING WELL SAMPLING RESULTS FOR MW-4 VOLATILE ORGANIC COMPOUNDS~~

~~Compound DATE ______3/17/83 6/22/83 9/25/83 3/21/85 7/31/86 9/16/87 7/7/88 2/22/90~~

Dichlorodifluromethane OBS OBS 55 16 28 6 <1 Vinyl Chloride 7 15 23 22 10 7 2 <1 Chloroetfaaue OBS 16 23 12 12 12 <1 Methylene Chloride 120 200 260 96 7 9 <1 <1 Trichlorofluoromethane 8 13 7 5 2 <1 <1 <1 1,1 Dichloroetnane 8 49 63 109 53 46 23 <1 Trans-l,2-Dichloroethane 1 4 5 62 27 32 4 <1 1,2-Dichloropropane <1 7 6 4 <1 Trichloroethene 2 9 5 18 13 9 3 <1 Tetrachloroediene 15 28 70 40 7 12 <1

~~GERAGHTY & MILLER, INC. TABLE 2-7 STATE SAMPLING RESULTS OF LEACHATE SEEPS AT THE BUSH VALLEY LANDFILL DURING 1986 - 1988~~

~~Compound Range (ug/L)~~

Chloroethane <1 - 17 Methyl ene Chloride 2 - 6000 Vinyl Chloride <1 - 2 Benzene <1 - 18 Toluene <10 - 2060 Ethyl benzene <1 - 110 Total Xylenes <2 - 310 Tetrahydrofuran <1 - 2130 2-Butanone (MEK) 29 - 5400 Methyl isobutylketone (MIBK) 9 - 300 Ethyl ether 1 - 650 Acetone 133 - 4660 2-Propanol 131 - 72000

~~Note: Detection limit represented by < symbol. The sampling method used was EPA Method 601. Source: MDE Files: State of Maryland Department of Health and Mental Hygiene (DHMH) Laboratory Results.~~

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~~AR302U85 Table 3-5 Summary of Environmental Samples Collected Daring the Third Sampling Event~~

~~SAMPLING LOCATIONS AND DATE BY SAMPLE MEDIA (2) Sample Sample 1 Grotxndwater Date Surface Water Date~~

~~GM2-LSS 03-10-93 SW2 03-12-93~~

~~GM3 03-11-93 SW8 03-12-93 :~~

~~GM4-LSS 03-10-93 SW9 03-12-93 GM3-REP 03-11-93~~

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~~Sample Leachate Date LI 03-11-93 L2 03-12-93 L3 03-11-93 L4 03-11-93 L5 03-11-93 L6 03-11-93 LFB 03-11-93 L3REP 03-11-93~~

~~(1) All samples were analyzed for TCL/TAL/TIC CLP constituents~~

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~~GERAGHTY & MILLER. M3 02^88 Table 4-0.5. Precipitation Data for Area Surrounding Bush Valley Landfill~~

ONE YEAR IN lfl(l> t WILL HAVE AVG.W MORE LESS Month TOTAL THAN ' THAN 1992 DEP 1993 C*> DEP MEAN^ '' JAN 3.10 5.4 13 0.82 -1.93 2.44 -031 2.75 FEB 321 4.6 i 1.6 1.94 -0.44 2.77 039 238 MAR - 3.98 53 1.4 4.09 0.66 5.69 226 3.43 APR 3.87 7.0 13 1.67 -126 4.95 2.02 2.93 MAY 3.86 7.8 13 230 -1.78 2.16 -232 4.68 JUN 3.70 5.8 13 239 -0.07 1.62 -134 2.96 ' JUL 433 6.7 1.4 4.79 035 339 -0.65 424 ' AUG 5.11 8.7 1.1 3.10 -036 2.02 -1.64 3.66 , SEP 3.96 7.0 0.6 4.17 -034 4.94 0.43 431 ; OCT 2.81 6.7 12 1.78 -0.80 __ __' 238 NOV 3.89 7.0 12 3.89 052 __ — _ 3.08 • DEC 4.01 7.0 0.9 331 0.61 ~" "~ — — 2.90 , YEAR 45.83 ' 54.60 36.6 35.55 435 __ — _ 40.10 • (1) Data from Bel Air, Harford County Maryland, August 1948 - December 1971, from USDA Soil Survey (2) Data from CSTA Meteriological Branch, Aberdeen Proving Ground, Spetsie Island. (3) Mean reflects monthly precipitation for period 1987-1993, DEP - Departure From Mean tTAB4.05/BUSH VALLEY/B70

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UPLAND FOREST: Acer rubrum. Red Maple. Abundant / codominant Betuia nigra.. River Birch. Infrequent. Carpinus caroliniana. Hop Hornbeam. Frequent. Carya glabra. Bitternut Hickory. Infrequent. Celastrus orbicularus. Oriental Bittersweet. Occasional. Cinna arundinacea. Stout Woodreed. Infrequent. Cornus florida. Flowering Dogwood. Occasional. Dennstaetia punctilobula. Hayscented Fern. Rare. Diospyros virginiana. Persimmon, Rare along wood edges. Dryopteris ^arthusiana. Spinulose Woodfern. Very rare. Eulalia viminia.. Nepal Microstegium. Occasional. Euonymus americana. American Strawberry Bush. Very rare. Fagus grandifolia. American Beech. Common / codominant. Fraxinus pensylvanica. Green Ash. Rare. Kalmia latifolia. Mountain Laurel. Infrequent. Lkmidamber styraciflua. Sweetgum, Abundant / codominant Uriodendron tulipifera. Frequent. Lonicera japonica. Japanese Honeysuckle. Abundant / codominant. Lycopodium digitatum. Fan Clubmoss. Infrequent. Nyssa sylvatica. Black Gum. Occasional. Onociea sensjbilis. Sensitive Fern. Infrequent. Quercus alba. White Oak. Infrequent. Ouercus falcate Spanish Oak. Rare, Ouercus palustris. Pin Oak. Common / codominant. Ouercus prinus. Chestnut Oak. Rare. Ouercus jcubra. Red Oak. Common / codominant Parthenocissus quinquefolia. Virginia Creeper. Common. Pinus virgfniana. Virginia Pine. Infrequent along wood edges. Polystichum acrostichoides. Christmas Fern. Occasional. Populus grandidentata. Big-toothed Aspen. Infrequent Prunus serotinq. Black Cherry. Very rare. Sassafras albidum. Sassafras. Occasional along wood edges. Toxicodendron radicans. Poison-ivy. Abundant / codominant Thelypteris noveboracengis. New York Fern. Frequent Vaccinium angustifolium. Lowbush Sweet Blueberry. Infrequent Vaccinium corymbosum. Highbush Blueberry. Rare. Viburnum prunifolium. Black Haw. Rare. t Viburnum recognitum. Northern Arrowwood. Abundant / dominant

PS \x\\ \ PR fMfr D ^ 0 9 li Q Table 4-3. List Of Plant Species (Continued) FLOODPLAIN FOREST: Acer negundQ. Boxeider. Abundant / codominant Acer rubrum.. Red Maple. Infrequent. Asarum canadense. Ginger. Occasional in colonies. Alliaria jastiolata. Garlic-mustard. Common. Arisaem^ triphyllum. Jack-in-the-pulpit. Occasional. Aster yimincus. Small White Aster. Occasional in open areas. Athvrium filix-femina ssp. michauxiii. Upland Lady Fern. Rare. Betula ru'gra. River Birch. Frequent. Boehmeria cylindrica. False Nettle. Infrequent. Carex alba. White Sedge. Very rare. Carya cordiformis. Bitternut Hickory. Rare along edges. Cinna arundinacea. Stout Woodreed. OccasionaL Cornus florida. Flowering Dogwood. OccasionaL Cornus amomum. Silky Dogwood. Occasional. Dryopteris carthusiana. • Spinulose Woodfern. Very rare. Duchesnea indica. Indian Strawberry. Abundant / codominant. Elymus virgmicus. Virginia Wild Rye. Infrequent Equisetum hyemale. Tall HorsetaiL Rare and locaL Euonymus alatus. Burning Bush. Very rare, one specimen. Fraxinus pensyivaru'ca. Green Ash. Abundant / codominant. Geum virginianum. White Aveus. Occasional. Glechoma hederacea. Ground-ivy. Common. Hemerocallis fulva. Tawny Daylilly. Locally abundant. Hesperis matronalis. Dame's Rocket Very rare, one specimen. Impatiens capensis. Spotted Jewelweed. Abundant codominant. Iris pseudacorus. Yellow Iris. Very rare. Juglans nigra. Walnut. Very rare. Laportea canadensis. Stinging Nettle. Abundant / codominant. Ligustrum ovaHfolium. Privet Very rare. Lindera benzoin. Spicebush. Abundant and dominant Lonicera japonica. Japanese Honeysuckle. Frequent near edges. Microstegmm vimineus.' Nepal Microstegium. Abundant / dominant Lindera benzoin. Spicebush. Common / dominant. Lonicera japonica. Japanese Honeysuckle. Frequent along edges. Lysimachia nummularia. Moneywort Common. Malus coronaria. Wild Crab. Very rare, one specimen. Nyssa sylvatica. Black Gum. Rare. Parthenocissus quinquefolia. Virginia Creeper. OccasionaL Pilea purnila. Clearweed. Rare. Platanus occidentalis. Sycamore. Common. Polygonum caespitosurr^ var. longisetum. Long-bristled Smartweed. Occasional along edges.

GERAGHTY & MILLER. t Table 4-3. List Of Plant Species (Continued) Polygonum cuspidatum. Japanese Knotweed. Infrequent in colonies. Polygonum punctatum. Dotted Smartweed. Infrequent. Poa sylyes. trfe. Woodland Bluegrass. Common. Ouercus palustris. Pin Oak. Infrequent. --—-- —-•- •--•• Parthenocissus quinquefolia.. Virginia Creeper. Occasional. Phalaris arundinacea. Reed Canary Grass. Rare. Ouercus palustris. Pin Oak. Infrequent. Rosa multiflora. Multiflora Rose. Infrequent along edges. Salix nigra. Black Willow. Infrequent. Toxicodendroq ra,dican§. Poison-ivy. Frequent. Tracaulon perfoliatum. Perfoliate Teanhumb. Occasional. Ulmus americana.. American Elm. Rare. Verbesina altemifolia. Wing-stem. Infrequent along edges. Viburnum recognimm. Northern Arrow-wood. Infrequent. Vinca minor. Periwinkle. Very rare, one colony. Viola papilionaceae. Common Blue Violet. Common.

HEDGEROW: Arthraxon .hispidus var. cryptanthus. Arthraxon. Locally abundant adjacent to thickets on east side of landfill (see open areas). Celastrug orbicularis. Oriental Bittersweet. Abundant and codominant Eupatoriadelphus fistulosus. Hollow Joe-pye-weed. Occasional Lom'cera japonica. Japanese Honeysuckle. Common. Microstegiurn yimineum. Nepal Microstegium. Abundant and dominant adjacent to many low thickets. Parthenocissus quinquefolia. Virginia Creeper. Common Rosa multiflora. Multiflora Rose. Abundant and codominant Rubus allegheniensis. Allegheny Blackberry. Common

FIELDS: Ambrosia aitemiisifolia. Common Ragweed. Frequent. Aster ericoides. Heath Aster. Common and dominant Bidens polylepis. Awnless Tickseed Sunflower. Occasional. Cyperus esculgn|us. Rare. Pgsmodium canescans. Occasional. Digitaria ischaemum. Smooth Crabgrass. Infrequent. 'Euthamia gramJneai. Flat-top Goldenrod, Abundant and dominant. Festuca a^rundfnacea. Common. Festuca elatior. Abundant and dominant. t Juncus effusus. Soft Rush. Rare.

GERAGHTY Table 4-3. List Of Plant Species (Continued) Lespedeza cuniata. Common. Pam'cum dichotomiflorum. Fall Panic Grass. Occasional. Pycnanthemum flexuosum. Narrow-leaved Mountain .Mint. Frequent. Rubus flagellaris. Dewberry. Occasional. Scirpus cvperinus. Wool-grass. Rare. Setaria faberu. Nodding Foxtail. Infrequent Solanum nigrum. Very rare. Solidago altissimum. Tall Goldenrod. Abundant and dominant. Triodea flavus. Purpietop. Occasional. SolidagQ nemoralis. Gray-stem Goldenrod. Occasional. Tvoha latifolia. Common Cattail. Rare

~~LAWNS: Lolium. spp. Ryegrass. Abundant codominate. Poa pratensis.. Kentucky Bluegrass. Abundant codominant Note: other grasses and herbs not identified due to the trimmed aspect of the lawn.~~

~~OPEN AREAS: No plant species list compiled due to the predominately bare soil aspect, but scattered plants do occur and are: the same species as in nearby field areas.~~

THE LANDFILL: Acer negundo. Boxelder. Rare in low areas at base of slopes. Agalinus purpurea. Late Purple Agalinus. Very rare in open areas. Andropogon virgim'cus. Broomsedge. Occasional with Aristida dichotomum. Apocynum. canabimim. Indian Hemp. Very rare. Aristida, dichotomy. Three-awn Grass. Abundant dominant on flat dry soils. Artemisia artemiisifolia. Common Ragweed. Occasional. Arthraxon hispidus var. cryptanthus. Arthraxon. Locally abundant adjacent to thickets on east border of the landfill. Aster lateriflora. Calico Aster. Rare in low thickets. Biden? polylepis. Awnless Tickseed Sunflower. Occasional. Celastrus orbicularis,. Oriental Bittersweet. Occasional in thickets. Cichorium intybus. Chicory. Very rare in open areas. Coroniila. varia. Crownvetch. Very rare on sothwest edge of fill. Dichanthelium clandestinurn. Deer-tongue. Rare. Dlgitaria ischaemurq. Smooth Crabgrass. Infrequent hi open areas on west side of landfill. t

GERAGHTY & MILL^S. &fi .2 ^ ^ 6 Table 4-3. List Of Plant Species (Continued) Dipsacus sylvestris. Teasel. Rare. Eragrostis spectabilis. Purple Love Grass. Rare. Eupatoriadelphus fistulosus. Hollow Joe-pye-weed. Infrequent in low swales and thickets. Eupatorium. pubescans. Hairy Thoroughwort. Rare in fields. Euthamia gramiriifolia. Flat-top Goldenrod. Common and dominant. Festuca arundinacea. Tall Fescue. Locally common on slopes. Fraxinus pensylvanica. Green Ash. Locally common near or at the bases of slopes. Gnaphalium obtusum. Cudweed. Infrequent. Juncus effusus. Soft: Rush. Rare on wet soils. Juncus lenuis. Path Rush. Common on paths, and damp areas. Juniperus yirgjniana. Red Cedar. Rare. Lespedeza. cuneata. Sericea Lespedeza. Occasional but mostly on grassy slopes. Liquidamber styraciflua. Sweetgum. Occasional, as seedlings and saplings. Lonicera japonica. Japanese Honeysuckle. Occasional on slopes. Melilotus .alka. White Sweet Clover. Infrequent. Malus zurnj. Flowering Crab. Very rare, two specimens. Pinus virginicus. Virginia Pine. Very rare in fields. Phragmites australis. Common Reed. Abundant and dominant in large colonies. Platanus occidentalis. Sycamore. Very rare, severaal saplings. Polvgonum punctatum. Dotted Smartweed. Rare in damp areas. Populus grandidentata. Big-toothed Aspen. Very rare, one sapling. Rhus copallina. Shining Sumac. Rare. Rhus toxjcodendrort. Poison-ivy. Frequent along banks and edges. Robmia pseudoacacia. Black Locust Common in small stands. Rosa multitlora. Multiflora Rose. Locally frequent in thickets on slopes along borders of the landfill. Rubus allegheniensis. Blackberry. Occasional in thickets. Salix nigyp. Locally common in low damp areas along the landfill borders. Scirpus arnericanus. Common, Three-square. Very rare, one small colony in seep on southwest side of landfill. Scirpus atrovirens. Green Bulrush. Very rare on wet soils. Scirpus cyperinus. Wool-grass. Locally common in wet areas. Setaria faberii. Nodding Foxtail. Infrequent. Solidago attissima. Tall Goldenrod. Abundant and codominant in field areas. Solidago rugosa. Wrinkle-leaf Goldenrod. Stachys tenifolia. Smooth Hedge-nettle. Very rare. Triodea Qava.. Purpletop. Infrequent in grassy areas. Tvoha latifolia. Common Cattail. Rare on wet soils.

GERAGHTY & Table 4-3. List Of Plant Species (Continued) NON-TIDAL MARSH: Mvosotori aquaticum. Giant Chickweed. Frequent. Phalaris arundinacea. Reed Canary Grass. Common. Polygonum pensylyanicum. Pennsylvania Smartweed. Abundant and codominant. Salix nigra. Black Willow. Frequent. Tracauion perfoliamm. Perfoliate Tearthum. Abundant and codominant. Tracaulpn. sagittatum. Arrow-leaved Tearthum. Abundant and codominant. Typha latifolia. Common Cattail. Infrequent.

SWAMPj Acer negundo. Boxelder. Rare. Acer nibrum. Red Maple.' Infrequent. .Acorus calamus. Sweetflag. Locally frequent. Betula nigra. River Birch. Infrequent. Carex strict^. Uptight Sedge. Occasional. Cephalanthus oqcidentalis. Buttonbush. Infrequent. Cornus arnQmum,. Silky Dogwood. Abundant / dominant Fraxinus pennsylvanica. Green Ash. Abundant / codominant Hibiscus moscheutos. Rose Mallow. Very rare. Ilex verticillata. Winterberry. Frequent. Iris pseudacorus. Yellow Iris. Frequent. Juncus effusus. Soft Rush. Rare. Ludwigia palustris. Water Purslane. Very rare. Lysimachia numrmilaria. Moneywort. Frequent Nuphai; adyena. Spadderdock. Frequent. Peltandra virginica. Arrow-arum. Locally frequent. Phalaris arundinacea. Reed Canary Grass. Locally common and codominant in lower, wetter areas. Polvgonum cuspidatum. Rare in colonies. Infrequent Polygonum. pensylvanicum. Pennsylvania Smartweed. Frequent. Qiiercus palustris. Pin Oak. Rare Rosa pahistris. Swamp Rose. Very rare. Salix nigr.a,. Black Willow. Locally common and dominant in lower wetter more open areas. Scirpus arngrjcanus. Common Three-square. Occasional. Smilax rotundifolia. Common Greenbriar. Frequent. Toxicodendron radicans. Poison-ivy. Common / dominant. Tracauion arifolium. Halbert-leaved Tearthumb. Locally abundant codominant in lower, wetter areas. Tracauion perfoliatum. Perfoliate Tearthumb. Occasional. Tracauion sagittatum. Arrow-leaved Tearthumb. Abundant / dominant

GERAGHTY & MILLER. Il)£ft 3 Q 2 ^ 9 9 Table 4-3. List Of Plant Species (Continued) ISOLATED WETLAND: Echinochloa cms-galli. Barnyard Grass. Rare. Juncus effusus. Soft Rush. Infrequent. Juncus canadensis. Canada Rush. Infrequent Panicum dichotomiflorum. Fall Witchgrass. Rare. Scirpus cvperinus. Wool-grass. Abundant and dominant Typha latifolia. Common Cattail. Frequent

GERAGHTY & MILLER, INC. fl R 3 Q 2 5 0 0 t Table 4-4. List of Animal Species MAMMALS: Blarina brevicaudfr. Short-tailed Shrew. • One road kill, and one live specimen seen in floodplain forest Didephus virginiana. Opossum. Spore seen in open area, tracks seen along stream in floodplain. Microtus peimsylvamcus. Meadow Vole. Several live specimens seen, many nests and tunnels seen beneath lumber debris in fields and open areas. Odocoileus virginianjj,s. White-Tailed Deer. Three live specimens seen and one fawn carcass seen, many tracks and spore seen in upland and floodplain forests, and open areas. Peromyscug leucopus. White-footed mouse. One live specimen seen beneath debris, several nests seen beneath rotting logs, spore seen in upland and floodplain forests. Procyon lojor. Raccoon, Several tracks seen bordering James Run in floodplain forest. Sciurus carolinensis. Gray Squirrel. Three live specimens seen in upland and forests, Silvilagus floridanus. Eastern Cottontail. Many h've specimens seen within and adjacent to the landfill, several spore samples seen in field areas.

GERAGHTY & MILLER, INC. R R 3 Q 2 5 0 I Table 4-4. List of Animal Species (Continued) Melospiza melodia. Song Sparrow. Songs heard, three live specimens seen in hedgerows and open areas adjacent to the landfill. Mimus polyglottis. Mockingbird. Three live specimens seen in hedgerow within the ____, landfill boundaries. Mniotilta varia. Black-and-white Warbler. One live specimen seen in floodplain forest ** Richmondena cardinalis. Cardinal. Four specimens seen in thickets and open areas near landfill. Spizella pjasserina. Chipping Sparrow. Several live specimens seen in hedgerow near the landfill Turdus migratorius. American Robin. Three live specimens seen in hedgerow and floodplain forest near landfill Vlreo olivaceous. Red-eyed Vireo. Call heard, one live specimen seen in floodplain forest bordering stream. ** Zenaida macroura. Mourning Dove. Three live specimens seen along floodplain forest edge. ** - Neotropical migrants

REPTILES: Carphophris amoenus. Eastern Worm Snake. One live specimen seen beneath lumber debris in open area adjacent to Bush Road. glaphe obsoleta. Black Rat Snake. One roadkill seen on Bush Road adjacent to upland forest. Thamnophis sirtalis. Eastern Garter Snake. One live specimen seen in open area of landfill.

AMPHIBIANS Ambystonia. maculatum. Spotted Salamander. One live specimen beneath debris in open area bordering Bush Road. Hyla crucifer. Spring Peeper. Several live specimens seen in swamp, Rana clamitans. Green Frog. Two live specimens seen, one in isolated pool and one on edge of fresh tidal marsh. Rana palustris. Pickerel Frog. Three live specimens seen in floodplain forest bordering James and Bynum Runs.

~~INSECTS: Acheta domestica. House Cricket Abundant in fields on the landfill and on the west side of Bush Road. Aedes sp. Mosquito. A few live specimens seen in floodplain forest and on landfill.~~

GERAGHTY & MILLER. INC. AR3Q2502 t Table 4-4. List of Animal Species (Continued) Green Darner. Two specimens noted, both near isolated pools. Bombus ameriocanomm. Bumblebee. One live specimen seen on Solidago altissima in field. Camponotiis sp., Crematogaster sp., Formica sp.. Ant Species. Abundant live specimens beneath debris, on open grounds, and La rotting logs throughout. Chalybion cajjifonugurny Blue Mud Dauber. One live specimen seen and nest seen in bluff on east side of the landfill. Colias philodic^. Clouded Sulphur. Two live specimens seen in field on west side of Bush Road. Ctenucha virginica. Orange-collared Scape Moth. One live specimen seen on Solidago altissima in field on west side of Bush Road. Danaus plexfppuj. Monarch Butterfly. Two specimens seen in field on west side of Bush Road. Dissosteira Carolina. Banded-wing Grasshopper. Four live specimens seen on open grounds on and near landfill. Gryllus pennsylyaniois. Field Cricket. Abundant in fields and on open grounds on the landfill, and on the west side of Bush Road. Hetaerina. americana. American Ruby Spot Two live specimens on vegetation on A landfilL Isia Isabella. Isabella Moth. Two larvae (woollybears) only seen on roadbank bordering Bush Road near field. Melanopus femurmbrurn. Red-legged Grasshopper. Abundant in fields and on open soils on the landfill, and on the west side of Bush Road. Neodiprion le'conteL Red-headed Pine Sawfly. Approximately a dozen live larva seen on Pinus virginiana at the lanfjfill- Papilio poly^enes astgrius. Black SwallowtraiL One live specimen in field. Popillia japonic,a. Japanese Beetle. One live specimen seen on vegetation en the landfilL. Pieris rapae. Cabbage Butterfly. Numerous live specimens seen in fields on landfill and on west side of Bush Road. Strongilirium sp. Darkling Beetle. Numerous specimens beneath debris in fields and on open grounds, both, on and off of the landfill. Tenodera aridofolia. Chinese mantid. One live specimen in field. Tibicen sp. Dog-day Cicada. Calls of several live specimens heard hi forests. Vanessa atalanta. Red Admiral Six live specimens seen on open grounds near and on landfill. Vespa crabro. Giant Hornet Several dozen live specimens seen in non-tidal marsh and on border of tidal marsh east of the landfilL Vespula m^culifrons. Yellow Jacket Two specimens seen on open grounds just west of the landfill.

r.PP AHHTV fi? Mil I FR ^302503 Table 4-4. List of Animal Species (Continued) MISCELLANEOUS TERRESTRIAL INVERTABRATES: Argiope sp. Argiope Spider. One live specimen in web in field. Helicodiscus sp. Land Snail. One live specimen beneath rotten log in upland forested area. Umax sp. Slug. Six live specimens beneath debris in open area and in forested area. Uthobius sp. Centipede. Two live specimens beneath debris in open area west of Bush Road. Lumbricus. terrestris. Earthworm. Abundant live specimens under debris in open and forested areas Lvcosa sp. Wolf Spider. Two live specimens beneath debris in field on west side of Bush Road. Micrathena, gracilis. Spined Orbweaver. Common live specimens in webs in forests throughout.

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~~3 a"~~

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~~Maximum Maximum Downwind Upwind [a] MEG t Constituents ^g/ta3) (Mg>rn3) (WJta3) (~~

Acetone 4.0 J 1.9 J 1,405 Benzene 1.7 16 71 Carbon disutfide U 13 143 Carbon tetrachloride 3.6 " , <0.014 30 Chloroform <0.15 0.12 J 23 Chloromethane <0.74 0.77 J 500 llthyi benzene 1.5 048 J 1.040 Methylene chloride 240J 106 J 619 Tetrachlorocthene 0.76 0.74 1495 Toluene 33 J 23J 843 L.l.l-Trichloroe thane 27 J 3.04 J 1,274 Trichlorocthene 88J 90J 1,274 Trichlorolluoromethane 1.8 J 0.86 NA Total xylenes . • 7.1J 1.68 J 1,040 [b]

d Upwind ambient air concentrations are used to represent background. b Value represents o— xylene isomer. MEG Multimedia Environmental Goal (USEPA. 1979). ug/m3 Micrograms per.cubic meter. J Estimated Value

~~308POR.WK1/BUSHVALLEY/B70~~

~~GERAGHTY & MILLER, INC. HR302538 Table 5-26. USEPA SW-846 8240 Volatile Organic Compound Results - Round 1, April 16, 1992~~

MEG* Upwind 1 Downwind I Downwind 2 Downwind 2 Upwm Scrici Collocated Compound fu/m1) (/tf/m5) pif/m*) (jig/m*) Gromochloromethane 'IS* IS LOW Chloromethane 500 0.019 ND 0.034 ND 0.034 ND 0.022 ND 0.043 ND 0.003 ND Bromomethane 142.6 0.010 ND 0.022 ND 0.022 ND 0.022 ND 0.022 ND 0.002 ND Vinyl Chloride 1200 0.010 ND 0.011 ND 0.022 ND 0.011 ND 0.022 ND 0.002 ND Chloroethane 6190 0.010 ND 0.022 ND 0.022 ND 0.022 ND 0.022 ND 0.002 ND Methylene Chloride 619 45.486 J 30.472 J 201.820 J 2.101 J 78.935 1 0.051 UJ Acetone 1405 1.943 J 3.955 J 2.146 i 0.079 UJ 0.108 J 1.332 J Carbon Disulfide 143 0.086 UJ 0.011 ND 0.225 UJ 0.011 ND 0.011 ND 0.001 ND 1.1-Dichloroethene 95 0.010 ND 0.011 ND 0.011 ND 0.011 ND 0.022 ND 0.001 ND 1,1-Dichloroethane 48 0.010 ND 0.011 ND 0.011 ND 0.011 ND 0.011 ND 0.001 ND irans-l,2-Dichloroeihene 95 0.010 ND 0.011 ND 0.011 ND 0.011 ND 0.011 ND 0.001 ND Chloroform 23 0.124 UJ 0.146 UJ 0.011 ND 0.011 ND 0.129 ND 0.001 ND 1,2-Dichloroethane 48 0.010 ND 0.011 ND 0.011 ND 0.011 ND 0.011 U 0.001 ND Trichlorofluoromethane NE 0.019 UJ 0.034 UJ 0.034 UJ 0.022 UJ 0.032 UJ 0.003 UJ cis-1.2-Dichloroelhene NE 0.010 ND 0.011 ND 0.112 UJ 0.011 ND 0.011 ND 0.001 ND 1,4-Difluorobenzene MS* IS LOW 2-Butanone 1405 0.095 UJ 0.146 UJ 0.157 UJ 0.124 UJ 0.161 UJ 0.016 UJ 1.1,1-Trichloroethane 1274 3.038 J 3.360 D 27.382 J 1.348 D 1.677 J 0.001 UJ Carbon Tetrachloride 30 0.010 ND 0.933 D 0.011 ND 0.011 ND 0.011 ND 0.001 ND Vinyl Acetate NE 0.010 UJ 0.011 UJ 0.011 UJ 0.011 UJ 0.011 UJ 0.001 UJ Bromodichloromethane 81 0.010 ND 0.011 ND 0.011 ND 0.011 ND 0.011 ND 0.001 ND 1.2-Dichloropropane 833 0.010 ND 0.011 ND 0.011 ND 0.011 ND 0.011 ND 0.001 ND cis-l,3-Dichloropropene NE 0.010 ND 0.011 ND 0.011 ND 0.011 ND 0.011 ND 0.001 ND Trichloroethene 1274 44.667 J 19.438 J 88.157 J 0.281 J 9.194 D 0.001 UJ Dibromochloromethane 81 0.010 ND 0.011 ND 0.011 ND 0.011 ND 0.011 ND 0.001 ND 1.1,2-TrichIoroethane 128 0.010 ND 0.011 ND 0.011 ND 0.011 ND 0.011 ND 0.001 ND Benzene 71.4 0.990 D 1.483 D 1.708 D 0.169 UJ 1.108 D 0.001 trans-l,3-Dichloropropene 20 0.010 ND 0.011 ND 0.011 ND 0.011 ND 0.011 ND 0.001 I| Bromoform 11.9 0.010 ND 0.011 ND 0.011 ND 0.011 ND 0.011 ND 0.001, Chlorobenzene-d5 «IS« IS LOV 4-Methyl-2-pentanone NE 0.010 UJ 0.011 UJ 0.011 UJ 0.011 UJ 0.011 UJ 0.0 2-Hexanone 29 0.010 UJ 0.022 UJ 0.022 UJ 0.022 UJ 0.022 UJ 0.002 ; Teirachloroethene 1595 0.152 J 0.539 J 0.573 J 0.011 ND 0.333 J 0.001 N'D 1, 1.2,2 -Tetrachloroethane 1 0.010 UJ 0.011 UJ 0.011 UJ 0.011 ND 0.011 UJ 0.001 UJ Toluene 843 15.000 J 33.169 J 6.326 J 0.303 J 23.032 J 0.035 UJ Chlorobenzene 830 0.010 ND 0.011 UJ 0.011 UJ 0.011 ND 0.011 UJ 0.001 ND Ethyl Benzene 1040 0.010 ND 0.011 UJ 0.011 UJ 0.011 ND 0.280 J 0.001 ND Styrene • 1000 0.010 ND 0.011 UJ 0.011 UJ 0.011 ND 0.011 UJ 0.001 ND o-Xylene 1040 0.010 ND 0.011 UJ 0.011 UJ 0.011 ND 0.333 J 0.001 ND ni/flr-XyJene NE 0.048 __J 0.079 __ J 0.011 UJ 0.022 UJ __ 0.763 J 0.003 UJ

D Indicates Detected Concentration. J Indicates Estimated Concentration. UJ Not Detected. Sample Quantitation Limit is Estimated. N D Indicates Not Detected, detection limit used for ambient concentration calculation. MEGs Multimedia Environmental Goals. NE Indicated None Established. Mg/rn5 Micrograms per cubic meter. IS Internal Standard.

~~, H-Feb-94 BVLRUNl.WKl/BUSHVALLEY/BTO 03:34 W* GERAGHTY 6? MILLER. INC. ^02539 Table 5-27. USEPA SW-846 8240 Volatile Organic Compound Results - Round 2, September 16, 1992~~

~~Downwind 2 Downwind Downwind 2 MEGs 1 Upwind 1 Collocated 2 Series Blank Compound fut/mM (tit~~

Bromochloromethane •IS' IS LOW IS LOW Chloromethanc 500 0.464 UJ 0.394 UJ 0.347 UJ 0.030 UJ 0.012 UJ Bromomethane 142.6 0.116 UJ 0.030 UJ 0.097 UJ 0.030 UJ 0.004 UJ Vinyl Chloride 1200 0.014 ND 0.030 ND 0.014 ND 0.030 ND 0.001 ND' Chloroelhane 6190 0.014 UJ 0.045 UJ 0.014 UJ 0.045 UJ 0.001 UJ Methylene Chloride 619 106.043 J 240.000 J 32.708 J 0.864 UJ 0.075 UJ Acetone 1405 1.449 J 0.515 J 0.861 J 0.030 UJ 0.001 UJ Carbon Disulfide 143 1.043 D 1.530 D 0.125 J 0.015 ND 0.001 ND 1,1- Dichloroethene 95 0.014 ND 0.030 ND 0.014 ND 0.030 ND 0.001 ND 1,1- Dichloroethane 48 0.014 UJ 0.015 UJ 0.014 UJ 0.015 UJ 0.001 UJ irans- 1,2- Dichloroethene 95 0.014 ND 0.015 ND 0.014 ND 0.015 ND 0.001 ND Chloroform 23 0.087 UJ 0.152 UJ 0.069 UJ 0.151 UJ 0.003 UJ 1 ,2 - Dichloroethane 48 0.014 ND 0.015 ND 0.014 ND 0.015 ND 0.001 ND Trichlorofluoromethane NE 0.406 UJ 1.258 J 1.792 J 0.167 UJ 0.037 UJ cis - 1,2 - Dichloroethene NE 0.014 ND 0.015 ND 0.014 ND 0.015 ND 0.001 ND 1,4 — Difluorobenzene "IS* IS IS 2-Butanone 1405 0.101 UJ 0.136 UJ 0.111 UJ 0.121 UJ 0.007 UJ 1.1.1-Trichloroethane 1274 1.464 J 1.015 J 1.111 J 0.439 UJ 0.001 UJ Carbon Tetrachloride 30 0.014 UJ 0.015 UJ 0.014 UJ 0.015 UJ 0.001 UJ Vinyl Acetate NE 0.014 ND 0.015 ND 0.014 ND 0.015 ND 0.001 ND Bromodichloromethane 81 0.014 UJ 0.015 UJ 0.014 UJ 0.015 UJ 0.001 UJ 1,2-Dichloropropane 833 0.014 ND 0.015 ND 0.014 ND 0.015 ND 0.001 ND cis — 1,3 — Dichloropropene NE 0.014 ND 0.015 ND 0.014 ND 0.0.15 ND 0.001 ND Trichloroethene 1274 89.623 J 39.652 J 6.000 D 0.242 UJ 0.001 ND Dibromochloromethane 81 0.014 UJ 0.015 ND 0.014 UJ 0.015 ND 0.001 UJ 1.1.2-Trichloroethane 128 0.014 ND 0.015 UJ 0.014 ND 0.015 UJ 0.001 ND Benzene 71.4 1.420 D 1.258 D 1.347 D 0.015 ND 0.001 ND trans - 1,3- Dichloropropene 20 0.014 ND 0.015 ND 0.014 ND 0.015 ND 0.001 ND Bromoform 11.9 0.014 ND 0.030 ND 0.014 ND 0.030 ND 0.001 ND Chlorobenzene-d5 •IS* IS IS 4-Mcthyl-2-pentanone NE 0.014 UJ 0.030 UJ 0.014 UJ 0.030 UJ 0.001 UJ ft 2-Hexanone 29 0.014 UJ 0.045 UJ 0.014 UJ 0.045 UJ 0.001 UJ Tetrachloroethene 1595 0.739 D 0.667 J 0.764 D 0.015 ND 0.001 ND 1 ,1,2,2 - Tetrachloroethane 1 0.014 UJ 0.030 UJ 0.014 UJ 0.030 UJ 0.001 UJ Toluene 843 5.377 J 3.970 J 4.194 J 0.136 UJ 0.015 UJ Chlorobenzene 830 0.014 ND 0.015 ND 0.014 ND 0.015 ND 0.001 ND Ethyl Benzene 1040 0.580 J 0.894 D 1.500 D 0.015 ND 0.001 ND Styrene 1000 0.014 ND 0.015 ND 0.014 ND 0.015 ND 0.001 ND o-Xylene 1040 . 0.478 J 0.909 D 1.694 D 0.015 ND 0.001 ND m/p — Xvlenc NE 1.203 J 2.515 J 5.403 J 0.015 UJ 0.001 UJ D Indicates Detected Concentration. J Indicates Estimated Concentration. UJ Not Detected. Sample Quantitation Limit is Established. ND Indicates Not Detected, detection limit used for ambient concentration calculation. MEGs - Multimedia Environmental Goats. NE Indicated None Established. Mg/m! Microgram* per cubic meter. IS Internal Standard. Note: Downwind 1 sample not available due to laboratory error.

BVLRUN2.WK3/BUSHVALLEY/B70 Table 5-28. 8240 Volatile Oragnie Compounds Results - Round 3, December 16,1992 MEG* > Upwind 1 Downwind 1 Downwind 1 Downwind 2 Blank t Series Compound (jif/m*} fyig/m31 (jifJm*} (jj,jJm3) (jig/m1} (jj.gJMmole') BromocfaJoromethane •IS* IS Chlorometfaane 500 0.767 J 0.521 UJ 0.738 UJ 0.609 UJ 0.018 J Bromometbane 142.6 0.110 UJ 0.123 UJ 0.138 UJ 0.130 UJ 0.004 J Vinyl Chloride 1200 0.014 ND 0.014 ND 0.015 ND 0.014 ND 0.001 ND Chloroethane 6190 0.014 ND 0.014 ND 0.015 ND 0.014 ND 0.001 ND Methylcne Chloride 619 72.260 J 20.534 J 28.862 J 9.072 D 0.004 UJ Acetone 1405 0.521 UJ 0.562 UJ 0.923 J 0.725 J 0.001 UJ Carbon Disulfide 143 2.342 D 0.616 UJ 0.738 UJ 0.333 UJ 0.003 UJ 1,1- Dichloroethene 95 0.014 ND 0.014 ND 0.015 ND 0.014 ND 0.001 ND 1,1 — Dichloroethane 48 0.014 UJ 0.014 UJ 0.015 UJ 0.014 UJ 0.001 UJ trans - 1,2 -Dichloroethene 95 0.014 ND 0.014 ND 0.015 ND 0.014 ND 0.001 ND Chloroform 23 0.123 J 0.123 ND 0.015 ND 0.145 ND 0.001 ND 1,2 - Dichloroetbane 48 0.014 ND 0.014 ND 0.015 ND 0.014 ND 0.001 ND Trichlorofluoromethane NE 0.863 D 0.795 D 0.662 J 0.826 D 0.001 ND cis - 1 ,2 - Dichloroethene NE 0.014 ND 0.014 ND 0.015 ND 0.014 ND 0.001 ND 1,4 - DiQuorobenzene •IS* 2-Butanone 1405 0.329 UJ 0.219 UJ 0.154 UJ 0.261 UJ 0.002 UJ 1,1,1-Trichloroethane 1274 1.247 D 1.014 D 0.138 J 1.101 D 0.001 ND Carbon Tetrachloride 30 0.014 ND 0.521 J 0.031 J 3.594 D 0.001 ND Vinyl Acetate NE 0.014 ND 0.014 ND 0.015 ND 0.014 ND 0.001 ND Brom'odichloromethane 81 0.014 ND 0.014 ND 0.015 ND 0.014 ND 0.001 ND 1,2— Dichloropropane 833 0.014 ND 0.014 ND 0.015 ND 0.014 ND 0.001 ND cis - 1,3 - Dichloropropene NE 0.014 UJ 0.014 UJ 0.015 UJ 0.014 UJ 0.001 UJ Trichloroethene 1274 20.822 J 1.767 J 4.508 J 2.101 J 0.001 UJ Dibromochloromethane 81 0.014 ND 0.014 ND 0.015 ND 0.014 ND 0.001 ND 1, 1,2-Trichloroethane 128 0.014 ND 0.014 ND 0.015 ND 0.014 ND 0.001 ND Benzene 71.4 2.589 D 1.425 D 0.862 J 1.580 D 0.001 ND trans - 1,3 -Dichloropropene 20 0.014 ND 0.014 ND 0.015 ND 0.014 ND 0.001 ND Bromofonn 11.9 0.014 ND 0.014 ND 0.015 ND 0.014 ND 0.001 ND Chlorobenzene— d5 •IS* 4-Methyl-2-pentanone NE 0.014 UJ 0.014 UJ 0.015 UJ 0.014 UJ 0.001 UJ 2-Hexanone 29 0.014 UJ 0.014 UJ 0.015 UJ 0.014 UJ 0.001 UJ Tetrac hi oroet hene 1595 0.233 J 0.192 J 0.015 ND 0.217 J 0.001 ND 1 , 1,2,2 -Tetrachloroethane 1 0.014 UJ 0.014 UJ 0.015 UJ 0.014 UJ 0.001 UJ Toluene 843 3.014 J 1.986 J 1.585 J 2.420 J 0.033 UJ Chlorobenzene 830 0.014 ND 0.014 ND 0.015 ND 0.014 ND 0.001 ND Ethyl Benzene 1040 0.384 UJ 0.315 UJ 0.108 UJ 0.348 J 0.003 J Styrene 1000 0.219 UJ 0.151 L'J 0.277 UJ 0.203 UJ 0.002 UJ o-Xylenc 1040 1.603 D 1.178 J 0.954 J 1.449 D 0.009 UJ m/p-Xylene NE 0.479 UJ 0.370 UJ 0.215 UJ 0.435 J 0.003 J D Indicates Detected Concentration J Indicates Estimated Concentration. UJ Not Detected. Sample Quantitation is Eiti mated. ND Indicates Not Detected, detection limit toed (or ambient concentration calculation. MEGs Multimedia Environmental Goals. NE Indicated None Established. fig/m1 Microframs per cubic meter. IS Internal Standard.

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~~~~Federal~~~~

Chemical-specific Safe Drinking Water Act (SDWA) RCRA Groundwater Protection Standards Federal Ambient Water Quality Criteria Clean Water Act - NPDES Requirements EPA Drinking Water Health Advisories Clean Air Act - NESHAPS Toxic Substance Control Act Location-specific Executive Order 11988 on Floodplain Management and Wetlands Executive Order 19990 on the Protection of Wetlands 40 CFR Part 6 Appendix A: Statement of Procedures on Floodplain Management and Wetland Protection Action-specific Federal SDWA Discharge to Groundwater Requirements (Re-injection of Treated Groundwater) Federal Hazardous andNonhazardous Wastewater Management Standards (On-site/Off-site Disposal of treated soil) Federal NDPES Stormwater Runoff Requirements (Discharge of Treated Groundwater to Storm Sewer or Surface Water Body) Federal Air Emission Standards for Hazardous Air Pollutants (including NESHAPS and Discharge of Air from. Air Stripper) EPA Effluent Guidelines for Organic Chemicals (Groundwater Treatment) Water Appropriation or Use (COMAR 08.05.02)

~~~~State~~~~

Chemical-specific Quality of Drinking Water in Maryland (Code of Maryland Regulations [COMAR] 26.04.01) Disposal of Controlled Hazardous Substances (COMAR 26.13.01 through 26.13.09) Water Pollution (COMAR 26.08.01 through 26.08.08) Air Quality (26.11.01 through 26.11.21)______(Continued)

GERAGHTY & MILLF-R, INC. AR30255! TABLE 6-1 (Continued) PRELIMINARY LISTING OF POTENTIAL ARARs t Location-specific Chesapeake Bay Critical Area Commission Criteria for Local Critical Area Program Development (COMAR 14.15.01, .02, .04, .07, .09, .10 & ,11) Chesapeake Bay Critical Area Commission - Development in the Critical Area Resulting from State and Local Programs (COMAR 14,19.01, .03 & .05) Action-specific Erosion and Sediment Control (COMAR 26.09.01) Well Construction (COMAR 26.04.04) Solid Waste Management (COMAR 26.04.07) Board of Well Drillers (COMAR 26.05.01) Storm Water Management (COMAR 26.09.02)

~~~~TBL6-1. W/BUSHVALLEYr.BSS t~~~~

~~~~SR302552 GERAGHTY & MILLER, INC.~~~~