PRELIMINARY PUBLIC HEALTH ASSESSMENT
MAGNOLIA CITY LANDFILL
MAGNOLIA, COLUMBIA COUNTY, ARKANSAS
Magnolia City Landfill is an active municipal landfill located near
Magnolia, Arkansas. Aluminum hydroxide sludge 
and liquid hazardous
wastes, primarily consisting of organics and solvents, are among
the different types of waste materials which have been accepted by
this landfill since the mid-1950's. Past waste disposal practices
included burning liquid waste and placing the residual in a
disposal pit, and pouring liquid waste into drums which were later
buried. On-site ground water is contaminated with lead, chromium,
benzene, and possibly vinyl chloride. Approximately two dozen
households are located within a 1-mile radius of the site. Some of
these households may depend on ground water for drinking or
domestic purposes. Monitoring has indicated lead and zinc
contamination in two residential wells. The source of this
contamination has not been determined. Although ingestion or
inhalation of contaminants in the ground water from the site would
be a public health concern, whether this is occurring or could
occur is unknown. Therefore, it is not possible based on the data
provided to evaluate the long-term public health threat raised by
the site. Exposure pathways of indeterminate public health concern
include ingestion of and inhalation of contaminated ground water.
The Magnolia City Landfill is an indeterminate public health hazard because a risk to human health may exist from possible exposure to hazardous substances at concentrations that may result in adverse human health effects. ATSDR has recommended that an environmental health education program be conducted to advise the public health professional and local medical communities of the nature and possible consequences of exposure to contaminants at the Magnolia City Landfill. This program has subsequently been provided by ATSDR, in cooperation with the Arkansas Department of Health. In addition, ATSDR will contact the EPA and the Arkansas Department of Health to alert them of the potential for exposure to contaminated water from private wells in off-site areas and to help determine appropriate future actions.
This document has been made available for Public Comment. As a result of comments received by ATSDR, the document has been altered to reflect publicly stated concerns regarding the document. Appendix 1 contains further information regarding Public Comments.
A. SITE DESCRIPTION AND HISTORY
The Magnolia City Landfill site, located in Magnolia, Columbia County, Arkansas, is 80 acres, with 40 acres being used as a landfill (see figures 1 and 2). The City of Magnolia received a permit in November 1975, from the Arkansas Department of Pollution Control and Ecology, to operate this site as a solid waste disposal facility. The landfill presently continues to accept residential, commercial, and industrial waste from the entire county of Columbia.
During the period from 1955 through 1979, Magnolia City Landfill received approximately 95,700 gallons of liquid waste, containing organics and solvents, from Firestone Coated Fabrics Company. Prior to 1974, approximately 56,100 gallons of this waste was burned and the residual buried. The remaining 39,600 gallons of the waste was placed in drums and buried between the years 1974-1979. Some of these drums were reportedly smashed by landfill operators when the burial area was covered.
Magnolia City Landfill also received approximately 37,450 cubic yards of aluminum hydroxide sludge from the Alumax Aluminum Corporation, Magnolia Division (formerly the Howmet Aluminum Corporation). The volume of waste transported to the landfill by Alumax has reportedly been reduced by 88 percent since 1983. The U.S. Environmental Protection Agency (EPA) has noted evidence of illicit dumping at this site.
The Magnolia City Landfill was proposed to the EPA's National
Priorities List (NPL) on October 25, 1989. The EPA subsequently
reevaluated the groundwater usage in the three mile radius around
the site and determined that all the residents in the affected area
have access to municipal water with minimal hook-up requirements.
Because an alternate unthreatened source of groundwater is
available, the rank of this site fell below the cutoff score for
listing on the NPL. Consequently, the site was dropped from NPL
consideration on August 28, 1990.
Agency for Toxic Substances and Disease Registry (ATSDR) representatives visited the site in January 1990. During this site visit it was learned that, in contrast to municipal waste, which is crushed and covered each day with a layer of soil, the aluminum hydroxide sludge is deposited in piles which are levelled periodically. The landfill is unfenced and accessible. The gatekeeper stated that the landfill is not used for recreational purposes, although people occasionally trespass to scavenge through the municipal waste. One scavenger was noted on the site during the site visit. During a tour of the immediate area surrounding the site it was observed that flow in Hurricane creek was low.
C. DEMOGRAPHICS, LAND USE AND NATURAL RESOURCE USE
The area around the site is rural and sparsely populated. An estimated two dozen households are located within a one-mile radius of the site. The closest residence is located approximately one-quarter mile from the site boundary. Approximately 630 students in kindergarten through the second grade live within a 4-mile radius of the landfill.
Houses near the site may be served by one of three community water systems or may rely on their own private wells for water. A population of approximately 12,000 people inhabit the area which at least one of these three water systems are able to serve. Sixty-five to seventy-five percent of the residents use community supplied water. According to Mr. Wheatley, Mayor of the City of Magnolia, and the EPA, 100 per cent of all residents in the affected area have access to either the Dorcheat Water System of the Walker Water System with minimal hook-up requirements (1). It is unclear how many households potentially impacted by the site use private well water for domestic purposes. Many of the households which have municipal water also have a private well which residents may use for watering gardens, watering livestock, washing cars, and possibly for drinking water (see figure 3).
No recreation or other raw water usage is known in nearby Hurricane and Nations creeks. There are seasonal variations in the level of flow in these intermittent streams. As previously stated, the level of flow was observed to be low during the site visit in January 1990.
Magnolia City Landfill is surrounded by woods and residential areas. There is no significant irrigation of crops. Limited hunting of squirrel occurs in the area near the site. Major natural resources include oil, gas, and timber.
D. STATE AND LOCAL HEALTH DATA
ATSDR has identified the following state and local health data sources as potentially pertinent to this site:
The first two documents are generated through the Arkansas State Department of Health. The vital statistics are analyzed down to the county level. Although a cancer registry was begun in early 1970's, the information gathered was incomplete and unreliable. Efforts to continue the registry ceased in the early 1980's; it has not been functioning for the past ten years (2). An independent research group at a major hospital has been monitoring fetal loss and birth defects in central and southern counties of Arkansas (2). No additional independent studies related to health effects of the population around the Magnolia City landfill have been identified.
Residents living in the Walker Water Association service area in the vicinity of the site have reportedly requested connection to municipal water out of concern about potential site-related ground-water contamination (3). A resident of this area indicated to ATSDR representatives (4) that some neighbors attributed headaches and stomachaches to the contaminated water. In addition, the resident indicated that neighborhood cancer deaths might be attributable to the contaminated water. No additional citizen's concerns or disease occurrences related to the Magnolia City Landfill were discovered during the site visit or through subsequent phone calls to state and local health departments.
ENVIRONMENTAL CONTAMINATION AND OTHER HAZARDS
The environmental characterization data was taken from two EPA documents, the Expanded Site Inspection (5) and the Hazard Ranking System report (6). A search through the Toxic Chemical Release Inventory (TRI) for the years 1987 and 1988 did not identify any facility in the Magnolia City Landfill zip code area with reported releases of contaminants of concern at the site.
On-site sampling of ground water, surface water, soil, air, and wastes was conducted in March 1987 and February 1988. In July 1987, ground-water and drilling soil samples were collected at on-site monitoring wells. These wells were resampled in September 1987.
Organic vapor analyzers and HNU photoionizers were used to conduct on-site air monitoring. The instrument readings were all within the background range (0-5 parts contaminant per million parts air [ppm]) and did not identify any elevation of volatile or vapor concentrations.
All other media were analyzed for the presence of contaminants listed on the Hazardous Substances List. With the exception of ground water, the levels of contaminants in these media were not of public health concern.
Ground-water samples drawn from the seven monitoring wells located along the perimeter of the landfill were found to have high levels of inorganic contaminants. Monitoring well #4 also contained elevated levels of organic contaminants.
In July 1987, slightly elevated levels of lead were detected in each of the monitoring wells, except for wells #2, #7 and #8.
Values of lead concentration were reported as unusable from samples collected during September 1987. In February 1988, a ground-water sample from monitoring well #4 was analyzed and again indicated an elevated lead concentration. As can be seen in Table I, elevated levels of chromium were detected in each of the monitoring wells. It was detected in monitoring wells #3, #7, and #8 in both July and September 1987, and in well #4 on September 1987 and February 1988. Samples taken from monitoring well #4 also indicated high concentrations of benzene and trichloroethylene (TCE) during each sampling event. In September 1987, vinyl chloride was detected in monitoring well #4 (see Table I).
Ground-water, surface-water, soils, and sediment samples were collected off the site in March 1987 and February 1988. The media in which elevated levels of contaminants were detected are ground water and surface water. In March 1987, elevated levels of zinc were detected in two and lead in four residential wells. Also at this time, lead was detected in surface-water drainage pathways. The February 1988 effort reported no lead concentrations above detection limit in the four wells. Only one of the residential wells initially reporting elevated levels of zinc was resampled. For this well there was a dramatic reduction in the concentration (see Tables II & III).
C. QUALITY ASSURANCE AND QUALITY CONTROL
In preparing this Preliminary Public Health Assessment, the ATSDR relies on the information provided in the reference documents and assumes that adequate data quality assurance and quality control (QA/QC) measures were followed with regard to chain-of-custody, laboratory procedures, and data reporting. The validity of the analysis and the conclusions drawn in this Preliminary Public Health Assessment are determined by the reliability of the referenced information.
Data Gaps and Inconsistencies
The information provided to the ATSDR does not include data from each monitoring and residential well for each sample date. The data from September 1987 for lead is reported as unusable because it extended beyond control limits. In February 1988 only monitoring well #4 was resampled. It is not possible to completely characterize the plume of contamination in the ground water using available data.
Consistency in the setting of detection limits is also of concern. Lead was not detected in any of the samples drawn from residential wells during the February 1988 sampling round. This, however, may be a result of the detection limit used to analyze the samples. For this particular batch of samples a detection limit of 30 micrograms per liter (ug/L) was used. Thirty ug/L is below the current Maximum Contaminant Level (MCL) of 50 ug/L but above the proposed MCL (PMCL) of 5 ug/L. A detection limit of 5 ug/L was however used to analyze for lead in surface water samples. As ingestion of lead contaminated ground water is a primary exposure pathway, an appropriate detection limit at or near the PMCL should be used when analyzing for lead in this media.
Critical Evaluation of Data
The composition of waste materials deposited in landfills may allow for the production of methane, a highly explosive gas. Although the existence of buried drums could not be verified (3) by magnetometer surveys conducted on site, their potential presence increases the possible physical hazard.
A. ENVIRONMENTAL PATHWAYS (FATE AND TRANSPORT)
Soil/Sediment
The surficial aquifer under Magnolia City Landfill is contaminated. Although the current data does not indicate elevated levels of contaminants in the soil, conditions at the site support the possibility that contaminants may have leached from the soils and wastes into the aquifer. The general environmental characteristics of the soil and the presence of chemicals which enhance transport increase the potential for migration of contaminants through soil layers into the aquifer.
Soil type, soil composition, permeability and water retention capacity can greatly influence the transport of contaminants through soils. There are two types of sandy loam soils in this landfill. Loam is a rich soil composed of clay, sand, and some organic matter. The western side of the site contains Smithton soil which is normally found on upland flats, exhibits low natural fertility and organic content, and is acidic. The soil has moderate to low permeability and medium available water capacity. Because this area is poorly drained the ground tends to be wet several days following a precipitation event. The soil found on the eastern two-thirds of the landfill where the disposal pit is located is called Sacul series. It is also acidic, but has lower permeability and higher available water capacity than the Smithton soil. It drains moderately well, but has the tendency to shrink and swell with climatic changes.
Methane tends to migrate through the soil and eventually rise to the surface. A pipeline runs northeast across the southern end of the landfill. If methane is being produced it could migrate along the path of this pipeline. Volatile organic compounds (VOC's) have been observed to have an affinity to methane gas and therefore could be transported with the gas. Due to the type of soil at and around the site it is likely that methane and the VOC's would exit to the surface before reaching the distance at which residences exist. Therefore, explosion near residential areas is not likely to occur.
Materials such as the aluminum hydroxide sludge deposited along the southern border of the site contain small percentages of other metals such as lead. The acidic property of the soils at this landfill could facilitate lead migration from the sludge through the soil layers. Thus, it may be possible that through infiltration lead could leach through the soil layers and into the ground water. The potential for lead, chromium and zinc to migrate along a soil pathway may be further increased by the presence of acidic materials which may have been disposed of at the landfill.
The organic content of the soil is also a very important factor in determining whether lead and other metals will have a greater tendency to adsorb to soil or migrate down through the soil layers and into the aquifer. Generally, metals are more mobile in soils containing less organic matter. As previously indicated, the soils at this sight are low in organic content.
Chromium is most often found in the +3 [Cr(III)] or +6 [Cr(VI)] oxidation states. Cr(VI) is more mobile than Cr(III), which usually becomes adsorbed or complexed to soil particles, metal oxides, or organic matter and is therefore usually relatively immobile. Cr(VI) has a tendency to be reduced to Cr(III). In a low organic soil CR (VI) is less likely to be reduced; but in an acidic environment mobility of Cr(III) can be increased. Thus, it appears that chromium, whether in the +3 or +6 oxidation state, may be mobile in this environment.
Zinc is usually found in the +2 oxidation state. It can be found as a hydrated ion, a metal-organic complex, or a metal-inorganic complex in water. In acidic soils, zinc absorption to soils is related to the availability of cation exchange sites. Because there are other mobile metals present, competition for the binding sites will occur, and zinc too may be mobilized.
It appears that VOC's will also be mobile in this environment. Volatilization would be limited for contaminants discharged into subsurface soil, but transport from the soil to the ground water would be expected to occur fairly easily.
Ground Water
The Cockfield Formation is the affected aquifer. The Cockfield is part of the Claiborne Group which is composed of sand, clay, and silt layers. The Claiborne is a part of the larger Gulf Coastal Plains aquifer system. An important regional characteristic of these aquifers is that recharge is chiefly accomplished by vertical infiltration and in some places from surface-water infiltration. The Cockfield Formation, Cook Mountain, and Sparta Sandstone are the major subdivisions of the Claiborne.
Residential wells draw from the Cockfield, which is composed of fine to medium grained sand and thin beds of lignite. Its maximum thickness is approximately 100 feet. The direction of regional ground water flow in the Cockfield is southeasterly. Because the site is on a topographic high, groundwater beneath the site flows radially outward primarily in the northeast, northwest and southeast directions. Water table levels are usually 15-20 feet below the surface but are very close to the surface (2-4 feet below) in winter and early spring.
The Sparta Sandstone, an important source of water for municipal water systems, lies 750 feet below the site and is composed of sand with clay or shale interbeds and localized lignite occurrences. Cook Mountain acts as a confining bed between the Cockfield and the Sparta Sandstone. It is composed of clay and shale with small amounts of sand. Its maximum thickness is approximately 280 feet and it is believed to be relatively impermeable.
On-site sampling has indicated the presence of heavy metals and VOC's in the surficial aquifer (the Cockfield Formation). Lead concentrations ranging from just below to just above the current MCL were detected in wells downgradient of the site. The highest lead and zinc values (99 ug/L and 15.4 mg/L) were detected off-site in an downgradient residential well located approximately two-thirds of a mile from the northern border of the site (well #12). There is a downgradient well approximately one quarter of a mile north of the site in which the concentration of lead was a little more than a third of the 99 ug/L maximum noted above (well #67).
Normally lead and other heavy metals are not soluble in water and are known to travel slowly through an aquifer. They may, however, form soluble complexes which will increase their propensity for migration through this medium. The site's ground-water contamination plume has not been adequately characterized; thus, given the limited data, a pathway between on- and off- site contamination cannot be established at this time.
Surface Water
Because the site is located on a topographic high, water flowing along natural drainage pathways could potentially contaminate off-site surface water. Hurricane Creek is a primary target lying half a mile south of the landfill. Lead was detected in a drainage pathway; but sampling thus far has not indicated that Hurricane Creek has been affected.
During the site visit it was observed that the creek was nearly dry. Seasonal variations in level of flow may affect migration of contaminants along this pathway. Until seasonal monitoring can document that this is not the case, surface water should not be ruled out as a potential pathway.
Air
No volatiles or vapors were detected at on-site sampling stations using direct reading equipment. The likelihood of airborne releases of contaminants are minimal because the VOC's were injected into a subsurface soil disposal pit. As previously mentioned atmospheric volatilization would be limited in such cases. Soil gas monitoring, a tool used to indicate whether underground vapors exist and if migration is occurring, was not conducted on- or off- site. Until such sampling is done a soil gas pathway cannot be ruled out.
Food Chain
It has been reported that limited squirrel hunting has occurred in the vicinity of the site. Lead concentrations are not elevated in the soil and according to the available data surface-water contamination is minimal. In light of this a food chain contamination problem via squirrels is not expected. Current users of contaminated ground water are reportedly not using that water for watering livestock. Therefore, exposure to contaminants through this foodchain entity is not expected. Future migration of contaminated ground water to residential wells where livestock is watered may require further investigation.
Available data indicate that human exposure to lead contaminated ground water may have occurred in the past (residential wells #12 and #67) or may still be occurring (residential wells #37 and #69) off the site via ingestion. The source of this contamination has not been determined. Individuals at the two residences where wells were identified as contaminated reportedly use that water for bathing, car washing and gardening only. Individuals at the two remaining residences reportedly use the water for drinking and domestic uses. Of those four homes only one was reportedly connected to municipal water at the time the EPA report was written.
The extent of the ground-water contamination plume and residential ground water use has not been fully characterized. It is unknown exactly how many residences use well water for drinking purposes because it has not been determined that all homes in the area have been connected to the public water system. Public water is available to the entire affected area. A risk of future exposure may exist if the groundwater plume is found to extend in the pathway of residential wells. If the water is used for drinking purposes, the exposure pathway of concern would be ingestion. The inhalation and dermal pathways become important if benzene, vinyl chloride, and other volatiles are carried with the plume. These chemicals will volatilize fairly easily from water especially when used in domestic activities such as cooking and showering.
Insufficient data preclude a complete characterization of human exposure to contaminated surface water and air, but available data indicate that this is not likely to be of concern. Available data indicate that human exposure to contaminated soil is not likely to be of concern.
Human exposure to lead from off-site residential wells (up to 99 ug/L) is of potential public health concern. Concentrations of lead above the EPA PMCL (5 ug/L) promulgated under the Safe Drinking Water Act have been detected in four out of nine residential wells sampled.
Lead toxicological studies only show health effects in humans at contamination levels higher than the highest level found around Magnolia City Landfill. Yet, most studies discuss information in terms of blood lead level rather than external exposure level. Therefore, the effects of lead on human health at the levels found around Magnolia City Landfill cannot be determined with certainty. The Centers for Disease Control has recently revaluated its guidelines on acceptable blood lead levels based on recent scientific information and studies (7). New data indicate that significant adverse health effects of lead exposure can occur in children at blood lead levels previously believed to be safe. Some health effects have been documented at blood lead levels as low as 10 ug/dl (7).
Blood lead concentrations of 10 ug/dl are associated with neurobehavioral deficits, hearing impairments, and inhibition of hemoglobin synthesis in children (7). Blood lead levels between 10-20 ug/dl in children have been shown to result in a four- to five-point decrease in the Intelligence Quotient (I.Q.), and in electrophysiological changes in brain activity. Blood lead concentrations greater than 33 ug/dl in children produce neurotoxic effects as well as a depression in plasma levels of Vitamin D. Neurotoxic effects of lead in children are of primary concern since those effects can be irreversible, even after blood lead levels return to a normal range (8).
Gastrointestinal symptoms are characteristic of lead poisoning (8); however, a dose-response relationship has not been explored. Headaches were not reported in the literature. No data on the association between human oral exposure to lead and cancer have been reported. Animal oral exposure studies suggest a qualitative relationship between exposure to lead in food and renal tumors. Human occupational inhalation data are inconclusive but suggest an increase in malignant neoplasms. The EPA has classified lead as a probable human carcinogen. Therefore, exposure to lead should be avoided at any level.
Human exposure to zinc at a private well off-site is of no apparent public health concern. Zinc is a metal naturally found in the earth's crust and is an essential nutrient required by the human body in low doses. When ingested in doses significantly higher than found at this private well, zinc is known to be toxic in humans. Levels found in this private well may result in human exposure to approximately twice as much zinc as is estimated to be the recommended daily allowance (RDA) for the average adult by the National Academy of Sciences (NAS). The level of zinc detected exceeds the USEPA Office of Water Regulations and Standards' Ambient Water Quality Criterion of 5 mg/L. However, this is a taste-based standard.
The minimum zinc exposure level associated with adverse human health effects is not known (9). Several studies have suggested that human ingestion of zinc may cause symptoms of gastrointestinal distress, however, dose levels could not be established. Gastrointestinal symptoms have been associated with the ingestion of various forms of zinc (e.g. zinc chloride, zinc sulfate); as the form of zinc detected in residential wells is not specified, application to this site cannot be determined with certainty. Headaches were not reported in the literature. Due to very limited and inconclusive animal data, an association of cancer with zinc ingestion cannot be established. Other effects noted in zinc health studies were associated with exposures to concentrations significantly higher than those found around the Magnolia City Landfill site.
In addition, if ground-water contaminants migrate from on the site to off, ingestion exposure to benzene, chromium and possibly vinyl chloride may occur.
B. HEALTH OUTCOME DATA EVALUATION
Information on Columbia county and Magnolia city has been collected for 1980-1985 by an independent research group at a major hospital in Arkansas. Investigators there report that both the county (Columbia) and the city (Magnolia City) have statistically significant elevated rates of fetal loss when compared to other counties and cities of south-central Arkansas (10). These rates remain elevated and the difference continues to be statistically significant even when adjusting for dissimilarity among the counties in maternal age and race. However, it is not known if mothers living near the landfill have an excess rate of fetal loss. Furthermore, the cause of the excess rate of fetal loss in Columbia County and Magnolia City cannot be determined from these data.
Based on available information, ATSDR has concluded that the Magnolia City Landfill is an indeterminate public health hazard because there is no evidence of exposure to any receptor population. Additional information is necessary to assess the potential for current exposure to site contaminants that might be migrating from the site. As noted in the Exposure Pathways Section of this Preliminary Public Health Assessment, exposure to elevated levels of VOCs and chromium may occur in the future via ingestion of contaminated groundwater. Additionally, exposure to elevated levels of lead may be occurring and may have occurred in the past via ingestion of contaminated water in off-site residential wells.
The ATSDR recommends the following:
This activity will be conducted by the ATSDR Division of Health Education in conjunction with the local medical community.
Based on data evaluated and the recommendations made by HARP, ATSDR has taken the following Public Health Action:
ATSDR in cooperation with the State of Arkansas Department of Health has provided environmental health education for the community to assist the community in assessing possible adverse health effects associated with exposure to hazardous substances. Literature on the effects of lead intoxication has been distributed to the state epidemiologist, local health clinics and physicians.
In addition, ATSDR will take the following Public Health Action:
ATSDR will contact the EPA and the Arkansas Department of Health to alert them of the potential for exposure to contaminated water from private wells in off-site areas and to help determine appropriate future actions.
Health Reviewer:
Stephanie Prausnitz
Environmental Health Scientist
Health Science Section
Remedial Programs Branch
Environmental Reviewer:
Rosalyn Lee
Environmental Health Engineer
Environmental Science Section
Remedial Programs Branch
ATSDR REGIONAL REPRESENTATIVE
Region VI Representative:
George L. Pettigrew
Field Operations Branch
Dallas, Texas
Figure 3. Residential Well Location Map
|
Monitoring Well #
|
||||||||||
| Max. Concentration in micrograms per liter (ug/L) | ||||||||||
|
1
|
2
|
3
|
4
|
5
|
7
|
8
|
MCL
|
PMCL
|
||
| Lead |
67J
(7/87) |
40J
(7/87) |
54J
(2/88) |
20J
(7/87) |
50
|
5
|
||||
| Chromium |
167
(7/87) |
202
(9/87) |
212
(9/87) |
227
(2/88) |
233
(2/88) |
663
(9/87) |
305
(9/87) |
50
|
||
| Benzene |
47
(7/87) |
5
|
||||||||
| Trichloroethene |
90
(9/87) |
5
|
||||||||
| Vinyl Chloride |
2J
(9/87) |
2
|
||||||||
| Sampling date in ( ) | ||||||||||
J: Value estimated
MCL: Maximum Contaminant Level (EPA)
PMCL: Proposed Maximum Contaminant Level (EPA)
Data Sources: ESI & HRS Documents
|
Residential Well #
|
|||||||
| Max. Concentration in micrograms per liter (ug/L) (3/87) |
|||||||
|
12
|
37
|
67
|
69
|
MCL
|
PMCL
|
SMCL
|
|
| Lead |
99
|
46
|
36
|
19
|
50
|
5
|
|
| Zinc |
15,400
|
2,300
|
23
|
61
|
5
|
||
MCL: Maximum Contaminant Level (EPA)
PMCL: Proposed Maximum Contaminant Level (EPA)
SMCL: Secondary Maximum Contaminant Level (EPA)
Data Sources: ESI & HRS Documents
Table III. OFFSITE SURFACE WATER
|
Corner of Site
|
|||
| Max. Concentration of Lead in micrograms per liter (ug/L) (3/87) |
|||
|
SE
|
NE
|
NW
|
|
|
20J
|
7.4J (Duplicate 56)
|
21.5J
|
|
J: Value estimated
Data Sources: ESI & HRS Documents
APPENDIX 1: RESPONSE TO PUBLIC COMMENTS
The Magnolia City Landfill Preliminary Public Health Assessment was available for public review and comment from July 1 through July 31, 1991. ATSDR received one written response pertaining to the Magnolia City Landfill Public Comment period. The commenter stated that the Preliminary Public Health Assessment "should reflect the fact that an alternate unthreatened source of ground water is available to all residents in the affected area." ATSDR has reviewed the available evidence. The Preliminary Public Health Assessment has been modified to reflect ground water availability.
