PUBLIC HEALTH ASSESSMENT
WAUCONDA SAND AND GRAVEL LANDFILL ENVIRONMENTAL
WAUCONDA, LAKE COUNTY, ILLINOIS
The tables in this section list the contaminants of concern. These contaminants have been evaluated in the subsequent sections of the health assessment for determination as to whether exposure to them has public health significance. These contaminants have been selected based upon the following criteria:
In the data tables that follow under the on-site contamination subsection and the off-site contamination subsection, the listed contaminant does not mean that it will cause adverse health effects from exposures. Instead, the list indicates which contaminants will be evaluated further in the health assessment.
The data tables include the following acronyms:
CREG: Cancer Risk Evaluation Guide EMEG: Environmental Media Evaluation Guide ILGWS: Illinois Groundwater Standards LTHA: Lifetime Drinking Water Health Advisory MCL: Maximum Contaminant Level MCLG: Maximum Contaminant Level Goal ppb: parts per billion ppm: parts per million RfD: Reference Dose RfC: Reference Concentration RMEG: Reference Media Evaluation Guide VOC: Volatile Organic Chemical
Comparison values for health assessment are contaminant concentrations in specific media that are used to select contaminants for further evaluation. Media levels for each chemical are compared with these values in the order in which they are explained below. The first value exceeded becomes the chemical-specific comparison value for the health assessment. These values include Environmental Media Evaluation Guides (EMEGs), Cancer Risk Evaluation Guides (CREGs), and other relevant guidelines that are commonly used. EMEGs are media-specific comparison values developed by ATSDR to select contaminants for further evaluation, derived from non-cancer health data. CREGs are estimated contaminant concentrations based on a one excess cancer in a million persons exposed over a lifetime. CREGs are calculated from USEPA's cancer slope factors. USEPA's Reference Dose (RfD) for noncarcinogens is an estimate of the daily exposure to contaminant that is unlikely to cause adverse health effects. The RMEG is calculated from the RfD, and is the concentration in water (assuming a person drinks 2 liters a day) that is unlikely to cause adverse health effects. The RfC is the actual concentration in air that is considered "safe" exposure. The USEPA developed the LTHA to provide the level of a contaminant in drinking water at which adverse non-carcinogenic health effects would not be anticipated with a margin of safety, over a period of 70 years, assuming exposure rate of 2 liters per day. Maximum Contaminant Levels (MCLs) are enforceable drinking water regulations that USEPA deems protective of human health (considering the availability and economics of water treatment technology) over a lifetime (70 years) at an exposure rate of 2 liters of water per day. MCLGs are non-enforceable drinking water health goals. They are set by USEPA at a level that no adverse health effects are anticipated to occur and which allow an adequate margin of safety. ILGWS are Illinois Groundwater Standards as set by the Illinois Pollution Control Board, which, if not met, trigger corrective action for potable water supplies. If the concentration of a chemical exceeds any of these values, it is selected as a contaminant of concern.
The contaminants of concern associated with this site are VOCs, metals, and a few semi-volatile compounds. The VOCs of concern are chlorinated solvents (alkanes and alkenes) including vinyl chloride, and benzene and 2-butanone. PCBs have been detected, only twice, at low levels in the USEPA/CRA sampling programs since 1983. Several pesticides were detected only once in 1983 in on-site groundwater, and have not been detected since. There are a number of metals of concern detected in on- and off-site upper aquifer samples. Antimony and vanadium were also present above comparison values in residential wells. Antimony is at similar concentrations in leachate, groundwater (on- and off-site) and in residential well samples. There is, therefore, no discernable concentration gradient linking antimony with the landfill. Vanadium has been detected at higher levels in leachate than in groundwater or residential wells. However, since it was also detected in Wauconda municipal wells which have not exhibited any other landfill-linked contamination, it is unclear whether vanadium present in the groundwater originated from the landfill.
Leachate
Sixteen samples of leachate were taken by USEPA in 1983 and Conestoga-Rovers Associates (1986-91). Table 1 shows the range of contaminant concentrations found in on-site leachate samples taken. One PCB (Aroclor 1260) was detected in one of 13 samples tested for PCBs in 1990 and one sample was found to have low levels of PCBs in 1992. PCBs were not detected in a duplicate sample taken a month later. In 1983, the USEPA collected samples from leachate seeps; in 1986, CRA collected samples from wells bored into garbage. From 1987 on, samples were obtained from the leachate collection system of the landfill. The LCHD sampled one leachate seep in 1987 for general water quality parameters and selected metals. No chemicals were found that exceeded health guidelines, although ammonia, iron, and chloride were elevated (LCHD, 1988).
Sediments
In 1983, Woodward Clyde Consultants obtained three sediment samples next to leachate seeps (USEPA, 1984). Only manganese was found to exceed comparison values.
Groundwater - Upper Aquifer Monitoring Wells
Monitoring wells were sampled by Woodward Clyde Consultants for USEPA in 1983-84. CRA sampled the wells for the WTG until 1987. No on-site upper aquifer samples have been taken since 1987 (CRA, 1990).
During this period, a number of metals were detected above applicable comparison values (Table 2). Total metal concentrations were obtained for all samples; dissolved metal concentrations
were also obtained for a few samples. Four inorganics (boron, lead, antimony, and vanadium)
were especially common above comparison values.
Table 1
| Contaminant | Ranges of levels-ppb (1983-1991) |
Ranges of levels-ppb (1992) |
|
Inorganics | ||
| Arsenic | ND-500 | -- |
| Boron | 230-23,000 | -- |
| Barium | 200-1420 | -- |
| Cadmium | ND-<330 | -- |
| Chromium | ND-<710 | -- |
| Manganese | 104-230,000 | -- |
| Nickel | ND-830,000 | -- |
| Lead | ND-1,710 | -- |
| Antimony | ND-24 | -- |
| Vanadium | ND-159 | -- |
| Zinc | 100-44,200 | -- |
Volatile Organic Chemicals | ||
| Methylene chloride | ND-14,000 | ND |
| Acetone | ND-180,000 | ND |
| trans-1,2-Dichloroethene | ND-730 | ND |
| 1,2-Dichloroethane | ND-790 | ND |
| 2-Butanone (MEK) | ND-22,000 | ND |
| Chloromethane | ND-<500 | ND |
| Vinyl chloride | ND-<500 | ND |
| 1,1-Dichloroethylene | ND-<700 | ND |
| 1,2-Dichloropropane | ND-<600 | ND |
| Trichloroethylene | ND-<500 | ND |
| Benzene | ND-<500 | 8.1 |
| Tetrachloroethylene | ND-<700 | ND |
Semivolatile Organic Chemicals | ||
| 4-Nitrophenol | ND-<620 | -- |
| bis(2-Ethylhexyl)phthalate | ND-<650 | -- |
| Dibenz(a,h)anthracene | ND-<650 | -- |
| Naphthalene | ND-<420 | -- |
| Pentachlorophenol | ND-<940 | -- |
| PCBs | ND-15* | ND-3 |
Table 2
: Range of Contaminant Concentrations for On-Site Groundwater (upper aquifer)| Contaminant | Range of levels-ppb (1983-1987) | Frequency of detects | Comparison Values (ppb) |
| Arsenic | ND-142 | 17/32 | CREG=0.02 |
| Beryllium | ND-6.0 | 3/32 | CREG=0.008 |
| Boron | ND-1,700 | 10/17 | EMEG=100 |
| Cadmium | ND-2.0 | 10/32 | EMEG=2 |
| Chromium (hexavalent) | ND-54 | 21/32 | RMEG=50 |
| Manganese | 20-2,140 | 2/7 | RMEG=50 |
| Nickel | ND-192 | 24/32 | MCL=100 |
| Lead | ND-450 | 24/32 | ILGWS=7.5 |
| Antimony | ND-56 | 7/32 | LTHA=3 |
| Vanadium | ND-577 | 18/32 | LTHA=20 |
| Selenium | ND-35 | 2/32 | EMEG=30 |
| Chloride | 5,400-600,000 | 25/25 | ILGWS=200,000 |
| Thallium | ND-2.1 | 1/32 | LTHA=0.4 |
| 1,2-Dichloroethane | ND-0.4 | 1/22 | CREG=0.4 |
| Vinyl chloride | ND-30 | 8/22 | EMEG=0.2 |
| Benzene | ND-16 | 9/22 | CREG=1 |
| *Tetrachloroethylene | ND-26 | 6/8 (1984) 0/14 (1985-91) | CREG=0.7 |
| 1,1,2,2-Tetrachloroethane | ND-4.8 | 1/22 | CREG=0.2 |
| Ammonia | ND-85,000 | 8/9 | EMEG=3,000 |
| Sulfate | 13,000-2,670,000 | 16/16 | MCL=400,000 |
| *bis(2-Ethylhexyl)phthalate | ND-24 | 4/22 | CREG=3 |
| *alpha-Benzene Hexachloride | ND-0.007 | 1/22 | CREG=0.006 |
| *Dieldrin | ND-0.006 | 1/22 | CREG=0.002 |
| *Heptachlor | ND-0.10 | 1/22 | CREG=0.008 |
| *Heptachlor epoxide | ND-0.026 | 1/22 | CREG=0.004 |
Ammonia and sulfate exceeded the LTHA. Two VOCs (benzene and vinyl chloride) exceeded comparison values when detected, and were detected in at least one-third of samples taken. Bis(2-ethylhexyl)phthalate was detected in four of 22 samples taken. Four pesticides were detected in one of 22 samples, during the 1983 sampling event.
Phthalates and methylene chloride are common laboratory contaminants. Some detects of these compounds in different media may be due to laboratory contamination of samples. Some blanks showed detectable amounts of these compounds, but not all blanks associated with samples showing positive detects for these compounds showed detectable readings.
No PCBs were detected in on-site upper aquifer monitoring wells. Chloride, often used as a plume marker for sanitary landfills, was detected in high concentrations on the landfill and north and east of the landfill (Figure 4) (CRA, 1992a).
Groundwater - Lower Aquifer Monitoring Wells
Two samples were taken in the only on-site lower aquifer well, in 1991 and 1992. Metal concentrations were similar to off-site lower aquifer wells, as were general water quality parameters. Trace amounts of two phthalates (total 6 ppb) were found in 1991. Chloride increased from 110 ppm in 1991 to 150 ppm in 1992. No VOCs were detected. Only bis(2-ethylhexyl)phthalate slightly exceeded comparison values. This chemical is known to be a common laboratory contaminant.
Air
Woodward-Clyde Consultants took on-site air samples using sampling pumps and Tenax tubes for gas chromatography/mass spectrometry (GC/MS) analysis. Samples were taken at vents and along traverses across the landfill. Twenty-four organic compounds were identified in the air. However, field blanks taken during sampling showed higher concentrations than most of the ambient air samples. In addition, it appears that the air was less contaminated downwind of the site (USEPA, 1984). The report concluded that the landfill did not materially impact air quality at the site. Because of these and other inconsistencies in the data, these data will not be discussed further.
In 1988, Weston-Sper took air samples on-site using Summa Tenax cartridges for GC/MS
analysis. Measurements were taken downwind of gas vents and at the leachate collection house,
as well as in gas vents. Readings downwind of gas vents, upwind of the site, and at the tank
house, were all less than or comparable to field or system blank readings. Therefore, these
results cannot be interpreted and are not reported here. Table 3 shows the range of 11 readings
taken in five gas vents on the landfill (Weston-Sper, 1988). The values for six compounds
greatly exceeded comparison values; the nine other compounds detected do not have comparison
Table 3
| Gas Vents | Range of levels- (ppb) (1983-1990) |
Comparison Values (ppb) | *ACGIH TLV-TWA, (ppb) |
| Vinyl Chloride | ND-6,920 | EMEG=2 | 5,000 |
| Trichlorofluoromethane | ND-474 | -- | 1,000,000 |
| Methylene chloride | ND-7,000 | CREG=0.6 | 50,000 |
| trans 1,2-Dichloroethene | ND-118 | -- | 200,000 |
| 1,1-Dichloroethane | ND-164 | -- | 200,000 |
| 1,1,1-Trichloroethane | ND-66.4 | -- | 350,000 |
| Benzene | 88.3-1,430 | CREG=0.03 | 10,000 |
| Trichloroethylene | ND-1,400 | -- | 50,000 |
| Toluene | 53.8-13,100 | EMEG=1,000 | 100,000 |
| Tetrachloroethylene | ND-2,270 | EMEG=9 | 50,000 |
| Ethylbenzene | 32-6,200 | EMEG=300 | 100,000 |
| m-Xylene | 83-9,580 | -- | 100,000 mixed isomers |
| o-Xylene | 25-3,250 | -- | 100,000 mixed isomers |
| Styrene | ND-200 | -- | 50,000 |
| meta Ethyltoluene | ND-979 | -- | -- |
| Methane (% by volume) | ND-67% | -- | Lower explosive limit=5.3% |
-------------------------
values. To evaluate possible site worker exposure, the highest measured concentrations in gas vents were compared to the Threshold Limit Values (TLVs) established by the American Conference of Governmental Industrial Hygienists (ACGIH). TLVs are airborne concentrations of substances which the ACGIH believes nearly all workers may be repeatedly exposed to, day after day, without adverse health effects. Most of the measurements inside the gas vents were below the TLV/TWA (ACGIH Threshold Limit Value for the workplace - Time Weighted Average) for the respective gases. Since these readings were taken in gas vents, this indicates that exposure to site workers will be negligible because of dilution of these gases after they are released into the atmosphere. A USEPA risk assessment based on these data indicated that there is insignificant to no increased risk of cancer to local residents from these gases. Total exposure of residents to gases from vents and diffusing into the air through the topsoil cannot be determined with the information collected thus far. In 1990-91, CRA measured methane from gas vents and leachate wells, and found concentrations of methane up to 62% by volume (CRA, 1991a), which exceeds the lower explosive limit for methane.
B. Off-Site Contamination
Surface Water
In November 1983, Woodward Clyde Consultants collected eight surface water samples off-site, which were sent to the USEPA contract laboratory program for analysis. They were analyzed for inorganics, pesticides, PCBs, VOCs, and semi-volatile organic chemicals (priority pollutant scan). The samples were taken from Mutton Creek (upstream, downstream, and near the site) and two surface ponds about 400 to 600 feet from the site. These surface ponds were found to have no chemical concentrations above levels of health concern. The downstream Mutton Creek sample had elevated levels of trichloroethylene and three pesticides: dieldrin, heptachlor, and heptachlor epoxide. Trichloroethylene was also present in leachate in higher concentrations and therefore may have come from the landfill. The pesticides, however, were not found in any leachate samples from the landfill. These pesticides may have resulted from agricultural activity (USEPA, 1984).
In 1986, CRA sampled surface water samples in Mutton Creek immediately upstream and
downstream of a major leachate seepage point along the north perimeter of the landfill. Trace
amounts of three VOCs (total 3.5 ppb) were detected downstream. No pesticides or PCBs were
detected either upstream or downstream (CRA, 1987). In 1987, the LCHD sampled Mutton
Creek upstream, adjacent to, and downstream of the landfill during the construction of the
leachate collection system after residual leachate overflowed into the creek during the
construction of this system. Ammonia, sulfate, and boron were found immediately adjacent to
the landfill in concentrations exceeding comparison values; sulfate was found at levels exceeding
these comparison values upstream of the site. The high sulfate level may have been due to
residual leachate that was spilled in the creek during the construction of the leachate collection
system (LCHD, 1988) (Table 4). It must be noted that most of the data in Table 4 was collected
before leachate seeps were repaired. In 1990, Mutton Creek was monitored by CRA in response
to a leachate release from the collection system. Trace amounts of chloromethane were found
both upstream and downstream of the site; no other VOCs were detected. Metals were detected
at similar concentrations upstream and downstream. There were no detections of base-neutral
extractables, pesticides, or PCBs (CRA, 1990). The LCHD also sampled Mutton Creek in May,
1990. There were elevated levels of phosphorus, nitrate, and several other parameters upstream
and in the north tributary that flows into Mutton Creek. This is thought to be due to fertilizer and
livestock practices, since the north tributary flows through agricultural land. None of these
measurements, or other measurements during this sampling round, exceeded comparison values.
In April 1991, Mutton Creek was sampled in response to a leachate release from a collection
sump, which did not appear to reach the creek. No VOCs were detected, and metals were at
similar concentrations upstream and downstream of the site (CRA, 1991). No chemicals were
found that exceeded ATSDR comparison values during this sampling round.
Table 4
| Location of Highest Amount | Contaminant | Range of levels-ppb (1983-1990) | Comparison Values (ppb) |
| Downstream | Trichloroethylene | ND-52 | MCL=5 |
| Downstream | Dieldrin* | ND-0.046 | CREG=0.002 |
| Downstream | Heptachlor* | ND-0.026 | CREG=0.008 |
| Downstream | Heptachlor epoxide* | ND-0.032 | CREG=0.004 |
| Upstream | Chloromethane | ND-48 | LTHA=3 |
| Upstream | Manganese | ND-404 | RMEG=50 |
| Mutton Creek Adjacent | Boron | 58-16,900 | EMEG=100 |
| Mutton Creek Adjacent | Ammonia | ND->100,000 | EMEG=3,000 |
| Mutton Creek Adjacent | Sulfate | 70,000-772,000 | MCL=400,000 |
Sediments
In 1983, Woodward-Clyde Consultants collected seven off-site sediment samples, five from Mutton Creek and two from nearby surface ponds. There were no elevated levels of contaminants at the upstream Mutton Creek site. Trace levels of methylene chloride were detected at all sampling locations, but is a suspected laboratory contaminant. There were no pesticides or PCBs found adjacent or downstream of the site in Mutton Creek. Trace amounts of acetone and 2-butanone were found immediately downstream of the site (USEPA, 1984). No contaminants were found at levels above comparison values.
CRA sampled sediments associated with surface waters in 1986 and found one VOC: toluene
(2.8 ppb downstream and 35 ppb adjacent to the landfill), below comparison values. Metals were
similar upstream and downstream of the landfill. No PCBs were found in sediments (CRA,
1987). In March 1990, Mutton Creek sediment samples were collected in response to a leachate
release from the collection system. No concentrations of VOCs or metals were detected above
comparison values; there were no detections of pesticides or PCBs (CRA, 1990). CRA sampled
Mutton Creek sediments again in April 1991 because of a prior leachate release from the leachate
collection system. No VOCs were detected; metal concentrations were again similar upstream
and downstream of the site (CRA, 1991).
Table 5
| Contaminant | Ranges of levels-ppm (1983-1990) | Comparison Values-normal child(ppm) |
| Antimony | ND-24.0 | LTHA=3 |
Soils
CRA analyzed soil from two off-site monitoring well boreholes (OW409 and OW410, Figure 5),
for metals, VOCs, pesticides, and PCBs in September-October 1986 (CRA, 1987). Depth of the
samples was unspecified, and is assumed to be of subsurface soil, because these are borehole
samples. Metals were similar to normal values found in soils in Illinois (Kelty, 1983). The soil
also has small amounts of chlorinated hydrocarbons (Table 6).
Table 6
| Contaminant Organics (ug/kg) | Ranges of levels (ppb), 1986 | ATSDR Comparison Values normal child (ppb) |
| 1,1,1-Trichloroethane | ND-76 | -- |
| 1,1-Dichloroethane | ND-19 | -- |
Groundwater - Upper Aquifer Monitoring Wells
There were a number of metals present above comparison values. A number of VOCs, pesticides and semi-volatiles were also present above comparison values. It is not likely that the pesticides came from the landfill, because none of them were found in any leachate samples. Their origin is likely from nearby agricultural activities.
The distribution of organics, metals, and chloride (a common marker for sanitary landfill plumes) did not show a clear pattern among the wells during the 1990 and 1991 sampling events. Well OW403 (east of the landfill; Figure 3) consistently had the most detects and highest concentrations for VOCs. However, wells OW412 and OW416, east and much closer to the site, had fewer hits for VOCs. There was no clear pattern as to metals concentrations among different wells. The wells (OW408, OW407, OW406, and OW413) close to and north or northeast of the landfill had the highest concentrations of chloride. This is consistent with an expected chloride plume that would result from the existing north-northeasterly groundwater flow direction in the upper aquifer.
A number of tentatively identified compounds (TICs) were detected in the 1986 sampling round
off-site in the upper and lower aquifers (CRA 1987). The identity of these needs to be confirmed
by GC/MS before the health effects attributable to these can be assessed.
Table 7
| Contaminant | Ranges of levels-ppb (1983-1991) | Ranges of levels-ppb (1992) | Frequency of detects (1983-1992) | Comparison Values (ppb) |
| Arsenic | ND-47.6 | ND-54 | 43/135 | CREG=0.02 |
| Boron | ND-5,100 | ND | 21/52 | EMEG=100 |
| Cadmium | ND-55 | ND | 30/122 | EMEG=2 |
| Chromium | ND-161 | ND-26 | 86/119 | RMEG=50 |
| Manganese | 2-5,140 | 13-161 | 118/118 | RMEG=50 |
| Nickel | ND-308 | ND-108 | 89/119 | LTHA=100 |
| Lead | ND-441 | ND-5.6 | 81/130 | ILGWS=7.5 |
| Antimony | ND-155 | ND | 33/117 | LTHA=3 |
| Vanadium | ND-200 | ND-9 | 33/119 | LTHA=20 |
| Zinc | ND-185,000 | ND-496 | 99/118 | LTHA=2,000 |
| Thallium | ND-3.8 | ND-2 | 8/117 | LTHA=0.4 |
| Mercury | ND-4.4 | ND-1 | 2/117 | LTHA=2 |
| Beryllium | ND-1.5 | ND | 2/119 | CREG=.008 |
| Chloride | 7,300-1,570,000 | 7,000-1,000,000 | 109/109 | ILGWS=200,000 |
| Chloroethane | ND-16 | ND-3 | 24/128 | --- |
| 1,1-dichloroethane | ND-7 | ND-1.5 | 7/128 | --- |
| Methylene chloride | ND-1,400 | ND | 46/136 | CREG=5 |
| Acetone | ND-1,300 | ND-5 | 32/127 | RMEG=1,000 |
| 1,2-Dichloroethane | ND-2.2 | ND | 12/137 | CREG=0.4 |
| 2-Butanone | ND-1,000 | ND-5 | 5/128 | --- |
| Vinyl chloride | ND-9.1 | ND-3 | 43/137 | EMEG=0.2 |
| 1,1-Dichloroethylene | ND-0.3 | ND | 1/137 | CREG=0.06 |
| Trichloroethylene | ND-51 | ND-2 | 21/136 | CREG=3 |
| Benzene | ND-22 | ND-7 | 21/132 | CREG=1.2 |
| Tetrachloroethylene | ND-18 | ND | 7/136 | CREG=0.7 |
| Ammonia | ND-85,000 | ND-150,000 | 29/137 | EMEG=3,000 |
| bis(2-Chlorethyl)ether | ND-5.6 | -- | 21/25 | CREG=0.03 |
| bis(2-Ethylhexyl)phthalate | ND-94 | -- | 31/85 | CREG=3 |
| n-Nitrosodiphenylamine | ND-52 | -- | 3/85 | CREG=7 |
| alpha-Benzene hexachloride | ND-0.026 | -- | 3/80 | CREG=0.006 |
| beta-Benzene hexachloride | ND-0.075 | -- | 2/82 | CREG=0.02 |
| delta-Benzene hexachloride | ND-0.02 | -- | 4/82 | --- |
| Dieldrin | ND-0.014 | -- | 2/84 | CREG=0.002 |
| Heptachlor | ND-0.14 | -- | 7/84 | CREG=0.008 |
| Heptachlor epoxide | ND-0.009 | -- | 1/84 | CREG=0.004 |
Groundwater - Lower Aquifer Monitoring Wells
In 1983, one lower aquifer off-site well (134 feet deep) was monitored by Woodward Clyde
Consultants (USEPA, 1984). Acetone and 2-butanone (1300 ppb) were detected, the latter was
above comparison values. Lead was also detected in an unfiltered sample, but an upgradient
background well sample contained lead at a similar concentration, so this was not deemed to be a
contaminant originating from the landfill. Three lower aquifer off-site wells were sampled by
CRA in 1986, 1987, 1988, 1990, and 1991. 2-Butanone was detected once in 14 samples during
this time at 26 ppb, below comparison values. Several metals and VOCs were detected at levels
above comparison values (Table 8). Different contaminants were found at relatively low levels
at the three off-site wells at different times. There was no apparent pattern to the detects among
the three wells (CRA, 1990; CRA, 1992a). It therefore cannot be determined from the data given
whether these contaminants originated from the landfill. No PCBs were detected in lower
aquifer samples.
Table 8
| Contaminant | Ranges of levels (ppb) (1983-1991) | Ranges of levels (ppb) 1992 | Comparison Values (ppb) | Frequency of detects 1983-1991 |
| Arsenic | ND-10.1 | ND | CREG=0.02 | 1/18 |
| Boron | ND-360 | ND | EMEG=100 | 3/12 |
| Cadmium | ND-5.0 | ND | EMEG=2 | 1/15 |
| Manganese | 74-1,140 | 7.3-104 | RMEG=50 | 15/15 |
| Antimony | ND-88 | ND | LTHA=3 | 1/15 |
| Vanadium | ND-63 | ND-5 | LTHA=20 | 7/15 |
| Zinc | 10-6,560 | ND-87 | LTHA=2,000 | 13/15 |
| Thallium | ND-3.8 | ND | LTHA=0.4 | 1/15 |
| Methylene chloride | ND-50 | ND | CREG=5 | 5/18 |
| 2-Butanone | ND-1,300 | ND | --- | 2/18 |
| Trichloroethylene | ND-9.6 | ND | CREG=3 | 5/18 |
| Benzene | ND-4.4 | ND | CREG=1 | 3/18 |
| bis(2-Ethylhexyl)phthalate | ND-23 | -- | CREG=3 | 5/10 |
| Pentachlorophenol | ND-4.4 | -- | CREG=0.3 | 1/10 |
| n-Nitrosodiphenylamine | ND-14.0 | -- | CREG=7 | 1/10 |
Groundwater - Residential Wells
Woodward-Clyde Consultants sampled 21 nearby residential wells in 1983. They found one that
was contaminated with a number of substances above comparison values (203A, Figure 6; Table 9). Two other wells had cadmium levels exceeding the EMEG for cadmium (G213 and G224).
Both G203 and G250 had vinyl chloride above comparison values. Both of these wells were no
longer used for residential water after 1984; G203 was subsequently used as an off-site
monitoring well. In subsequent sampling (1986-91 by CRA), organic compounds were not
frequently detected, and usually at values close to the lower detection limit (CRA, 1992a). The
LCHD also sampled residential wells for water quality parameters and selected metals (M. Kuhn
et al., 1986; LCHD, 1988; Olsen et al., 1989, 1990, 1991).
Table 9
| Contaminant | Range of levels-ppb (1983-1991) | Range of levels-ppb 1992 | Comparison values (ppb) |
| Boron ** | ND-1,340 | ND | EMEG=100 |
| Cadmium + | ND-8.10 | ND | EMEG=2 |
| Lead + | ND-153 | ND-4.2 | ILGWS=7.5 |
| Antimony | ND-58 | ND | LTHA=3 |
| Manganese | ND-137 | 5.2-119 | RMEG=50 |
| Vanadium | ND-39 | ND | LTHA=20 |
| Zinc + | ND-7,140 | ND-602 | LTHA=2,000 |
| Vinyl chloride * | ND-3.8 | ND-1.6 | EMEG=0.2 |
| Benzene + | ND-4.6 | ND | CREG=1 |
| bis(2-Chloroethyl)ether + | ND-5.7 | -- | CREG=0.03 |
| bis(2-Ethylhexyl)phthalate | ND-7.0 | -- | CREG=3 |
The number of compounds and the frequency of detections was considerably lower than for upper or lower aquifer off-site monitoring wells (Table 9). Metals results were less variable compared to monitoring wells since residential wells generally provide less turbid samples. Only three metals (antimony, vanadium, and boron) exceeded comparison values in sampling after 1984. Vinyl chloride was the only VOC to exceed comparison values after this sampling, and it was detected once (1989). Contamination of residential wells appears to be minimal from the landfill except for vanadium, since this element has appeared several times in residential and monitoring wells and is present at higher concentrations in the leachate. Antimony is present throughout the groundwater and leachate, but its level is not elevated in the leachate.
Groundwater - Municipal Wells
The Village of Wauconda has six municipal wells. Well #4, closest to the landfill (about 1000
feet southeast) gets its water from a deep (Cambrian-Ordovician) aquifer. The other five wells
are 1 to 1.5 miles from the landfill (southeast to southwest of the site) and are screened in the
bedrock aquifer. In 1988-89, all six wells were tested for VOCs as well as general water quality
parameters. No VOCs were detected except toluene at one well (1.5 ppb) and chloroform at two
wells (0.8 and 2 ppb). They were all below comparison values. There were no VOCs detected at
well #4, the closest to the landfill. It is very unlikely that the landfill will impact the municipal
wells screened in the bedrock aquifer because of their distance from the landfill, and because the
upper aquifer flows in a north-northeasterly direction, away from these wells. Also, well #4 will
not likely be affected because it is in a deeper aquifer and is not in the direction of flow from
either aquifer.
C. Quality
In preparing this health assessment, the IDPH relied on the information provided in the
referenced documents and assumed that adequate quality assurance and quality control measures
were followed with respect to chain-of-custody, laboratory procedures, and data reporting.
Sampling in 1983 through January 1985 was conducted by USEPA using their own quality
assurance procedures. March and May 1985 sampling was conducted according to a quality
assurance project plan (QAPP) written by CRA that was not reviewed by USEPA. Sampling
from September 1986 through April 1991 was done according to a QAPP written by CRA and
approved by USEPA. The CRA 1986 and August-December 1991 sampling was done according
to a revised QAPP (CRA, 1991b), which was also approved by USEPA. The validity of the
analyses and conclusions drawn for this health assessment is determined by the completeness and
reliability of the referenced information.
D. Physical
At the time of this health assessment, site access was restricted by a chain link fence surrounding
the whole site, with a locked gate at the northeast corner for vehicle access to the leachate
collection tank area. The gap observed underneath the fence during the February 29, 1992 site
visit has since been repaired. The only physical hazards on-site were the steep terrain of the
southwest corner of the landfill. The area immediately southwest of the landfill is an off-site
demolition dumping area with unrestricted access. Piles of large pipes, culverts, and other
construction materials present a physical hazard to children or others trespassing in this area.
Methane gas buildup, resulting in a potential for fire and explosion, occurs at some sanitary
landfills. In 1988, USEPA took soil gas samples around the landfill and found this not to be of
significant concern.
E. Toxic
Since the reporting of toxic chemical releases began in 1987, the USEPA has collected information on estimated annual releases of toxic chemicals by industry to the environment (air, water, land, or underground injection). These data are compiled and are retrievable through the on-line database, Toxic Chemical Release Inventory (TRI). The reporting years of 1987 to 1992 are currently available for review.
These TRI records were reviewed for reporting industries in the vicinity of the site. No
industries near the site (Village of Wauconda, zip code 60084 or within a one mile radius of the
site) reported releases of chemicals to the environment.
PATHWAYS
To determine whether nearby residents are exposed to contaminants migrating from the site, IDPH evaluated the environmental and human components that lead to human exposure. This pathways analysis consists of five elements: source of contamination, transport through an environmental medium, a point of exposure, a route of human exposure, and an exposed population.
Exposure pathways are identified as completed, potential, or eliminated. Completed pathways require that the five elements exist and indicate that exposure to a contaminant has occurred in the past, is currently occurring, or will occur in the future. Potential pathways, however, require that at least one of the five elements is missing, but could exist. Potential pathways indicate that exposure to a contaminant could have occurred in the past, could be occurring now, or could occur in the future. Eliminated pathways require that at least one of the five elements is missing and will never be present.
One completed pathway has been identified at this site to date: groundwater contamination of
two residential wells prior to 1984. These wells were not used after 1984 for residential
purposes.
A. Completed
Nearby Well Users/Groundwater (Upper Aquifer) Pathway
The groundwater pathway is complete for wells for two residences that had elevated levels of
several contaminants in 1983-4, including vinyl chloride and benzene (3.8 ppb and 4.6 ppb,
respectively) (Table 9). Residential use was discontinued for these wells after 1984. Since these
wells are located 200-300 feet east and downgradient of the landfill and were tapped into the
upper aquifer, they are likely to get some contamination from the landfill. Upper aquifer
groundwater, which flows in a north-northeasterly direction, has shown a consistent pattern of
elevated chloride in monitoring wells 1000 feet east-northeast of the landfill (Well OW414,
Figure 4), and almost as far north of the landfill. Scattered detects of VOCs and elevated levels
of some metals have also occurred in off-site monitoring wells in this area. Since there is no
clear gradient of these compounds as distance increases from the landfill, it is unclear whether
the chemicals originated there. Residents living in the houses serviced by these wells were likely
exposed to these chemicals in water via ingestion (drinking water), skin contact (washing hands
and showering), and inhalation (as a result of the chemicals volatilizing into the air during
showers and general water use). Presently, two other wells tapped into the upper aquifer are
currently being used as residential wells, about 1600 feet northwest of the landfill. Six other
wells (of the approximately 35 located within 1/4 mile of the landfill) are of unknown depth, and
therefore could be tapped into the upper aquifer. There is potential for residents using shallow
aquifer wells north or northeast of the landfill to be exposed to a number of different chemicals
that have been detected in off-site upper aquifer groundwater.
B. Potential
Nearby Well Users/Groundwater (Lower Aquifer) Pathway
There are about 35 residential wells located within 1/4 mile of the landfill. All but eight are known to be screened in the lower aquifer. The lower aquifer has had scattered readings of elevated levels of some contaminants (Table 8). This groundwater flows southwest (Figure 5) at an average velocity of 72 feet/year (CRA, 1992a). Occurrence of chemicals at the three off-site lower aquifer wells do not show the expected pattern related to the landfill, since the two wells that were upgradient had higher readings for more chemicals than the one downgradient off-site well and one down-gradient on-site well (Figure 5). A clay aquitard lies between the upper and lower aquifer. It separates the upper and lower aquifer throughout the vicinity of the landfill except for an area north of the landfill (around well OW418, Figure 3), where the upper and lower aquifers are interconnected. This is attributed to glacial erosion of the clay layer and appears to be local to this well. Soil data from neighboring wells (OW415 and OW419) found this clay aquitard to be present. The east-west extent of this interconnection is estimated to be 550 feet (CRA, 1992a). Except for this area, groundwater flow from the upper aquifer to the lower aquifer is supposedly retarded by the aquitard. However, the observed pattern of chemical "hits" in the lower aquitard may be the result of upper aquifer water seeping through the aquitard into the lower aquifer. If that were the case, then the people living in houses served by wells tapped into the lower aquifer could potentially be exposed via ingestion (drinking), skin contact (e.g. dish washing, taking showers), and inhalation (volatilization of organic compounds during showers). The potential receptor population in this case is 30-35 families living near the landfill.
Nearby Houses/Dust Pathway
Exposure of nearby residents or businesses to windblown dust is another potential path of human exposure. Before the cap was put on the landfill, there were areas of uncovered garbage. This was a potential pathway of human exposure to contaminants from the landfill via inhalation of dust particles. However, since the cap was installed, garbage has been covered and the cap well covered with grass and other vegetation. This makes windblown dispersal of contaminated fill from the landfill extremely unlikely in the present or future, though it may have occurred in the past.
Nearby Houses/Landfill Gases Pathway
Past, current, and future exposure pathways are possible from contamination of ambient air by the landfill. This may occur from on-site vents or from gases escaping from buried garbage directly through the topsoil on the landfill. Measurements have been taken in on-site vents (Table 3), but the volume of gases escaping from them or directly through the topsoil of the landfill is unknown. Nearby homes downwind of the landfill are the likely point of exposure to landfill gases in ambient air. Exposure to gases, if occurring, would be through inhalation. The receptor population are the families living in houses downwind of the landfill, primarily to the east of the landfill. It is not known how many people, if any, may be affected because the amount of gases escaping is unknown. The USEPA monitored ambient air in 1988, as did the WTG in 1993. Both air evaluations indicated no adverse health risk to nearby residents from landfill gas and found this potential pathway to be unlikely.
Subsurface migration of gases from the landfill to the basements of nearby homes is another potential pathway. This has been documented at many landfills, with loss of life due to fire and explosion. The potentially affected people are the residents of nearby houses and businesses. The potential routes of exposure for this pathway are inhalation and heat transfer (fire or explosion). In 1988, USEPA conducted soil gas sampling and next to the landfill and found this potential pathway also to be unlikely.
Recreational Waters/Users Pathway
In the past, leachate from the landfill has on occasion flowed into Mutton Creek along the surface of the ground. There also existed the possibility of leachate flowing through an eroded ravine on the north side of the landfill into Mutton Creek. However, no persistent contamination of either surface water or sediment downstream of the landfill have been indicated (Tables 4 and 5). Receptor populations may have been exposed through dermal exposure (such as the possible playing of kids in Mutton Creek). It is not known how big these receptor populations were, but they probably involved very few people. Present and future via this pathway is not likely because the present operation of a leachate collection system, inspections, and control. The eroded ravine, mentioned previously, has been rebuilt as Swale #1 and was designed to prevent leachate migration.
Site Workers/Trespassers Pathway
It is possible for workers or trespassers to inhale landfill gases coming from vents on-site or up
through the topsoil while they are present at the landfill. It is also possible for workers or
trespassers to have skin contact with soil or surface water on-site. In the past, leachate seeps
were another source of contamination available for skin contact or inhalation of vaporized gases
from the leachate. This pathway is unlikely to be completed now or in the future because (1)
there is a security fence around the site; (2) site workers at Superfund sites are trained in use of
appropriate protective clothing; (3) gas concentration in ambient air have not been measured
above background, and is therefore probably very low except in the immediate vicinity of the gas
vents.
PUBLIC
A. Toxicological Evaluation
This section discusses the available data about the chemicals that are in human exposure pathways at the Wauconda landfill. There is often little information about the health effects caused by low level environmental exposure. Most human exposure studies use information from industrial exposures, where the doses are much higher than exposure to contaminants from the Wauconda landfill. Industrial exposure data normally do not include precise information about the dose, the purity of the chemicals, their interactions with other substances, and the duration of the exposure. With these limitations, human exposure data will be used in the following toxicology section. Although animals do not necessarily have the same responses that humans show when exposed to toxic substances, animal experiments can be conducted under carefully controlled dosages and time periods. Accordingly, when human information is unavailable or limited, pertinent animal data will be incorporated into this section. Chemicals considered in this section were found in residential wells or were often detected in lower aquifer off-site monitoring wells, the main source for drinking water for private wells near the landfill.
I. Volatile Organic Chemicals (VOCs)
a. Benzene
Benzene has been detected in leachate, on- and off-site groundwater, and residential wells (in 1983 sampling only) above comparison values. Benzene is a known human carcinogen; leukemia is associated with long-term benzene exposure. The maximum reading for a residential well was 4.6 ppb (obtained in 1983, and not detected since in any residential wells). A person drinking water with this level of benzene over a 70 year lifetime would experience no apparent increased risk of contracting cancer. Long-term exposure to benzene at higher levels can also disrupt normal blood production and cause a decrease in important blood components.
b. Methylene Chloride
Methylene chloride was detected in off-site lower aquifer wells at concentrations of up to 50 ppb. It has been shown to cause liver and lung cancer in laboratory animals, but there is little or no data indicating that it does likewise in humans. Therefore, it is suspected, but not known, to be a human carcinogen. The highest concentration measured would pose no apparent increased risk of cancer if one drinks water with the highest concentration found every day for a lifetime of 70 years. Animals exposed to methylene chloride in food or water at much higher concentrations experienced changes in liver function.
c. Trichloroethylene
Trichloroethylene (TCE) has been detected in off-site lower aquifer monitoring wells at levels about twice the USEPA Maximum Contaminant Limit (MCL) of 5 ppb. The maximum level detected would not exceed ATSDR's intermediate oral Minimal Risk Level (MRL) which indicates that noncarcinogenic health effects are unlikely to occur at the that level of TCE found in the lower aquifer. Animal studies of intermediate length (14 to 365 days) with much higher levels of TCE have shown some liver toxicity; long-term animal studies with very high levels have also shown some kidney toxicity. At that same TCE concentration, exposure would pose no apparent increase in cancer risk.
d. Vinyl Chloride
Vinyl chloride has been detected at low levels (up to 10 ppb) in off-site groundwater, in two residential wells in 1983 (subsequently not used), and once after that (of 28 samples collected) in other residential wells. The highest concentration found in any residential well was 3.8 ppb. It was also detected inside a landfill vent as gas, slightly above the American Conference of Governmental Industrial Hygienists (ACGIH) Threshold Limit Value (TLV) of 5,000 ppb. Vinyl chloride is a known human carcinogen. This has been determined through studies of vinyl chloride workers exposed to much higher levels than present in groundwater or ambient air near the landfill. Long-term cancer studies have shown vinyl chloride to cause liver tumors in rats and mice. A level of 3.8 ppb in groundwater, the highest reading obtained there, would result in a low increased risk of contracting liver cancer, if one drank water from the residential well with the highest concentration over a lifetime of 70 years. Exposure estimates based on the highest level found in groundwater exceeds ATSDR's chronic oral MRL for children and adults. The MRL for vinyl chloride is based on the lowest-observed-adverse-effect level of 0.018 mg/kg/day, which caused an increase in certain types of cellular nuclei in animals. At slightly higher doses, animals have been shown to experience increased blood coagulation and an increase in blood collagen.
II. Semi-Volatile Organic Chemicals
a. Bis(2-chloroethyl)ether
This compound was found above comparison values only in residential wells during the 1983 sampling round. It has not been found since in any groundwater, residential well, or leachate samples. Therefore, the "detection" of this compound may have been an artifact resulting from poor laboratory technique in 1983. This compound can cause liver cancer in mice, so it may also be able to cause it in people. Exposure to 7 ppb, which was the highest level detected in residential wells, would result in a moderate increase in the risk of cancer, roughly twice the risk experienced from drinking from a municipal water supply. However, this risk estimate is very conservative, and the actual risk is much lower, since the chemical has not been detected in any media after 1983.
b. Bis(2-ethylhexyl) phthalate (DEHP)
DEHP has been detected in leachate and off-site monitoring wells, and also occasionally at low levels (up to 7 ppb) in residential wells. The average intake of DEHP from water supplies in the U.S. is 0.02 mg/day. Assuming that an average person drinks two liters of water a day, this means that people, on the average, get an equivalent dose that would be obtained from drinking water that contains 10 ppb of DEHP, if DEHP was not ingested at all from food. This chemical is known to be a carcinogen in animals, but there is inadequate evidence or no evidence of carcinogenicity in humans. The maximum concentration found in residential wells would pose an insignificant or no increased risk of contracting cancer from exposure to DEHP at this level. Long-term exposure of animals to much higher levels of DEHP has resulted in structural and functional changes in the kidney, similar to those seen in the kidneys of long-term dialysis patients.
III. Inorganic Chemicals
a. Antimony
This metal has been detected in leachate, groundwater (on- and off-site) and in residential wells. Maximum concentrations found have been similar among all these media. It is therefore questionable whether the landfill is the source of antimony in the area. It has been detected in residential wells at levels (up to 58 ppb) which is 20 times the USEPA Lifetime Health Advisory (LTHA). It is not known what effects, if any, that antimony exposure at these levels has on humans or animals. Rats that drank a much higher level, 2000 ppb, for 600 days, died sooner than rats not exposed. Humans who drank 19000 ppb of antimony, once, vomited.
b. Boron
Boron has been detected in leachate, groundwater (on- and off-site) and in residential wells at the Wauconda landfill. In residential wells, it has been found at levels up to 1,340 ppb, which is slightly more than twice the U.S. EPA's Lifetime Health Advisory (LTHA) of 600 ppb. It is not known what effects, if any, that long-term exposure to boron at these levels can cause. The only information available on long-term exposure to boron by the oral route is the following: rats that were given water with 880,000 ppb of boron for 70 days experienced changes in sperm count. Boron sometimes occurs naturally in groundwater at levels of up to 5,000 ppb.
c. Cadmium
Cadmium has been detected in leachate and in groundwater (both on- and off-site). In 1983, cadmium was found in three of 21 samples taken from residential wells, at levels up to 8 ppb. It has not been detected in residential wells since then. Two of the three wells where cadmium had been detected were taken out of service. Exposure to this concentration is four times the chronic oral MRL for cadmium. There is no information on what health effects, if any, result from drinking water with this level of cadmium for a long period of time. Eating or drinking higher levels of cadmium over a long time can lead to a buildup of cadmium in the kidneys. This causes kidney damage, and also causes bones to become fragile and break easily. Animals that eat or drink high levels of cadmium sometimes get high blood pressure, iron poor blood, liver disease, and nerve or brain damage.
d. Chromium
Chromium has been detected in leachate and groundwater above comparison values. The highest observed reading for off-site lower aquifer monitoring wells is 71 ppb. Exposure to this concentration exceeds the USEPA chronic oral RfD for the hexavalent (VI) oxidative state of chromium, which is the most toxic. In fact, total chromium was measured, of which only a part is the (VI) form; the other common form is the trivalent (III) oxidative state, which is believed to be an essential nutrient. Therefore, there are unlikely to be any health effects associated with exposure to chromium, even at the highest level found in the lower aquifer. Ingestion of much higher amounts can result in stomach upsets, ulcers, and kidney and liver damage.
e. Lead
Lead has been detected in leachate, on- and off-site groundwater, and once above comparison values in a residential well (in 1983; 153 ppb) near the Wauconda landfill. Lead is considered to be a no-threshold toxin, which means that it is considered toxic at any level. The most sensitive population for lead exposure is the developing fetus and young children up to 6 years of age. The most detrimental effects are on the developing nervous system, which can result in behavioral effects, learning problems, and decreased IQ at low doses. Lead is also detrimental to the hematopoietic, cardiovascular, kidney, and immune systems. Health effects from lead toxicity from wells around the landfill is slight because 38 of 40 readings since 1983 have been below the Illinois Groundwater Standard of 7.5 g/L. These two readings were found in two different wells at different times, and are judged to be isolated occurrences.
f. Vanadium
Vanadium has been frequently detected in leachate, groundwater (both on- and off-site), residential wells, and once in the Wauconda municipal water supply, at concentrations exceeding comparison values. Since it appears to be ubiquitous in all these media and is not more concentrated in leachate, it does not appear to originate from the landfill. Vanadium has been detected in residential wells at up to 39 ppb, which is twice the USEPA Lifetime Health Advisory of 20 ppb. There is no information on what health effects, if any, exposure to vanadium at these levels may cause. Small amounts of vanadium normally occur in food and water. Most of this is poorly absorbed by the digestive tract. Animals that drink water with high levels of vanadium did not have an excess of tumors, but some minor birth defects occurred in the fetuses of female rats fed vanadium in water when they were pregnant. It is not known if these birth defects would occur in people. Minor effects on the kidney were seen in rats after exposure to high levels of vanadium for three months. Humans given 0.47 to 1.3 mg vanadium/kg body weight (the equivalent of 16,450 to 45,000 ppb of vanadium in water, assuming a daily intake of two liters per day and a body weight of 70 kilograms) did not show any altered kidney parameters.
g. Zinc
Zinc has been detected in leachate, off-site monitoring wells, and in residential wells (1983 sampling only) at levels exceeding comparison values. It was not detected in on-site upper aquifer monitoring wells. In residential wells, the highest reading was 7,140 ppb in one well in 1983, which is almost four times the USEPA Lifetime Health Advisory (LTHA). After 1983, there were no readings exceeding the LTHA. There is no data on what health effects that long-term exposure to this level of zinc in drinking water may cause, if any. Zinc is a natural mineral in many drinking waters, and average zinc intake in the diet ranges from 7-16 mg per day. Zinc is an essential nutrient, with a Recommended Daily Allowance (RDA) of 15 mg per day, and it is in many mineral supplements. If one obtained all of the RDA from water and drank two liters per day, the water would contain 7,500 ppb of zinc. Therefore, it is unlikely that any health effects would result from drinking water that had levels contained in the residential well with the highest concentration. If large doses of zinc (10 to 15 times the RDA) are ingested for a short time, stomach and digestive problems may occur.
B. Health Outcome Data Evaluation
Cancer Incidence data
The Division of Epidemiologic Studies of the Illinois Department of Public Health compared the observed number of cancer cases for the two zip codes nearest to the Wauconda landfill (Wauconda 60084 and Island Lake 60042) to the expected number of cancer cases. The expected number of cases is based on the cancer rate in a population similar in size and age distribution to these two zip codes.
In the 1985 to 1987 time period, 174 cases were observed (expected number 102). A statistically significant excess was identified in the age group 45 to 74 in both zip codes. In zip code 60042, this excess was attributable to males with lung or bladder cancer and to females with liver (hepatocellular carcinoma) or breast cancer. In zip code 60084, the increase was attributable to males with bladder cancer and females with cancer of the oral cavity.
None of these cancers has been shown to be associated with environmental exposure to chemicals detected at the landfill. Lung cancer is the leading form of cancer in the United States. Cigarette smoking may contribute to at least 80% of lung cancers in males. The remaining incidence may be due to occupational exposure by inhalation of asbestos, radon, mustard gas, polycyclic aromatic hydrocarbons, and other chemicals. Cigarette smoking also increases a person's risk of bladder cancer, as does occupational exposure to benzidine, 2-napthylamine and other aromatic amines used in dyestuffs. Rubber workers and tire makers have also exhibited an excess of bladder cancer; excessive use of analgesic drugs containing phenacetin has also been shown to increase risk. Eight of the 10 bladder cancer cases had a prior history of smoking; one had an occupational history with potential exposure to materials known to cause bladder cancer.
Breast cancer is associated with increasing age, family history of breast cancer, and a number of other factors. No scientific evidence exists between any environmental exposure and risk for breast cancer. Liver cancer is linked with cirrhosis (linked with excessive alcohol consumption). Angiosarcoma is a rare type of primary liver cancer linked to workplace exposure to vinyl chloride. Low levels of vinyl chloride were found in groundwater at the site and off-site. However, the one case of liver cancer found was hepatocellular carcinoma, not angiosarcoma. Known risk factors for cancer of the oral cavity include tobacco use, alcohol use, and nutritional deficiencies (iron and vitamins). Of the four female cases of cancer of the oral cavity, one used alcohol, one did not, and two had unknown histories of alcohol and tobacco use.
C. Community Health Concerns Evaluation
We have addressed each of the community concerns about health as follows:
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