MARINE SHALE PROCESSORS, INC.
AMELIA, ST. MARY PARISH, LOUISIANA
ENVIRONMENTAL CONTAMINATION AND OTHER HAZARDS
A. ON-SITE CONTAMINATION
On-site contamination of air, water, and soil has resulted and could still result from MSP operations. Stack emissions, fugitive organic vapor emissions from waste handling and processing, and blowing soils and dusts are primary examples of potential on-site air contamination. Rainwater percolating through on-site soils, and present and past storage of wastes or produced primary and slagged aggregate, could affect the groundwater underlying the site. Similarly, site soils may be contaminated from past waste storage practices or spills, leaks, or seepage. Rainfall that runs off site may also be contaminated while on site. With the exception of undisturbed, in-situ soils, all other identified contaminated media can be expected to migrate off site.
During MSP's operation, EPA, MSP, and LDEQ have on numerous occasions sampled the media identified previously. Throughout this period, there have been process and facility changes that would be expected to affect environmental sampling results. Each medium will be addressed individually to ease understanding of potentially affected exposure pathways. Numerical data presented in both on-site and off-site contamination tables contain, unless otherwise noted, the maximum contaminant level values found in a search of all data in ATSDR's possession. Many of those data points are below levels of health concern; however, they are included to allow the reader to see the full range of values considered by the Agency. If the reader is aware of additional data that represent even higher contamination levels, those data should be brought to the attention of ATSDR for further consideration.
AIR: The most obvious and commonly recognized potential for contamination of on-site air is the discharge of process exhaust gases and particulate through the smokestack (R-14, R-44, R-45, R-56, R-73). Since 1985, the degree of contamination of this effluent stream has been characterized by several stack tests conducted by facility contractors; some of which were monitored by EPA. Criteria pollutants such as nitrogen oxides, sulfur dioxide, carbon monoxide, and particulates have been analyzed for. Also, destruction and removal efficiency (DRE) -- a measure of hazardous waste destruction performance -- of selected species of hazardous material fed to the process kiln has been analyzed for. Other potential contaminants of concern analyzed for include arsenic, barium, cadmium, lead, chromium, mercury, hydrogen chloride, dioxins, and polycyclic aromatic hydrocarbons (PAHs).
Table 1 compares stack emissions of the criteria pollutants in 1985, 1988, and 1990. Table 2
compares stack emissions of selected metals in 1985, 1988, and 1990. The significance and fate
of these pollutants are discussed in the Environmental Pathways section of this public health
assessment.
| Table 1 | ||||||
| Marine Shale Processors, Inc.
Stack Emissions of Criteria Pollutants (lbs/hr) | ||||||
| 1985 | 1988 | 1990** | ||||
| Avg. | Max. | Test 1 | Test 2 | Avg. | Max. | |
| Nitrogen oxides | 19.44 | 19.94 | 27.1 | 37.7 | 66.3 | 68.0 |
| Particulates | 9.35 | 16.01 | 37.62 | 1.31 | 1.8 | 3.0 |
| Sulfur dioxide | 53.05 | 84.71 | 28.8 | 2.5 | <7.0 | 6.6 |
| Carbon monoxide | <100 ppm* | 18.8 | 0.3 | 1.0 | 2.3 | |
| *ppm = parts per million as reported
** MSP Compliance Test for Certification with Boiler and Industrial Furnace Requirements, June 20-23, 1990. Reference: D-100 | ||||||
| Table 2 | |||||
| Marine Shale Processors, Inc.
Stack Emissions of Select Metals (lbs/hr) | |||||
| 1985 | 1988 | 1990 | |||
| Avg. | Max. | Test 1 | Test 2 | Max.* | |
| Arsenic | <0.00020 | NR | 0.004 | <0.000772 | 0.006 |
| Barium | <0.055 | NR | 0.005 | 0.005 | NR |
| Cadmium | <0.228 | NR | 0.001 | 0.000473 | 0.00013 |
| Lead | <0.00097 | NR | 0.012 | 0.013 | 0.005 |
| Chromium | <0.063 | NR | 1.466 | 0.011 | 0.004 |
| Mercury | 0.0017 | 0.0044 | 0.016 | 0.013 | 0.048 |
| Nickel | NR | NR | 1.423 | 0.017 | 0.005 |
| * MSP Compliance Test for Certification with Boiler and Industrial Furnace Requirements, June 20-23, 1990.
NR = Not Reported Note: < means that the metal analyzed for was below the detection level shown. Reference: D-100 | |||||
In 1988, MSP conducted stack tests for the DRE of three hazardous organic feed constituents: trichloroethylene, dichlorobenzene, and carbon tetrachloride. The compounds selected for DRE testing are usually representative of feed materials that are most toxic, most difficult to burn, and/or most prevalent in the expected feed mix. If the MSP process kiln were regulated under hazardous waste incineration standards, it would have to meet a DRE of 99.99%, which means that less than 0.01% of the hazardous constituent in the feed mix would be allowed in the effluent stack gases. That regulatory approach to demonstrating adequate hazardous waste destruction and removal is based upon the assumption, and some observation, that by carefully selecting worst-case or most challenging chemicals to test for DRE, other less challenging compounds will also be successfully processed whenever 99.99% DRE is achieved. However, that approach does not necessarily ensure that all other non-feed products of incomplete combustion (PICs) in stack emissions will be insignificant. PICs could include partial breakdown products of the parent waste feed compounds, as well as recombinant new species that may be as or more toxic than the original waste constituents. See the discussion on dioxins for further information.
MSP demonstrated greater than 99.99% DRE during test runs for trichloroethylene and dichlorobenzene, but not carbon tetrachloride. The relatively low levels of carbon tetrachloride in the feed mix and the limits on the level of detection of carbon tetrachloride in the stack emissions could have prevented accurate DRE determination. Difficulty in calculating DREs for low-level feed constituents has been described in the literature on hazardous waste incinerator testing (R-30, R-31).
A similar DRE calculation dilemma was reported by MSP in 1985. DREs were analyzed for four PAHs fed at levels ranging from 85 lbs to 250 lbs per hour. DREs for all four PAHs were greater than 99.99%. Three other compounds, benzene, methylene chloride, and toluene, were fed at rates ranging from 0.049 lbs to 0.434 lbs per hour. None of the DREs for those compounds met the 99.99% criterion. In June 1990, DREs were analyzed for monochlorobenzene and carbon tetrachloride. All runs of all tests met and exceeded the 99.99% criterion.
When halogenated organic compounds are burned in the MSP kiln, it is expected that hydrogen chloride (HCl), an acid gas, will be formed. In 1985, MSP determined that emission levels of HCl were less than 2.5 lbs per hour. In 1988, emission levels of HCl ranged from 51.6 lbs to 416.3 lbs per hour. That increase was believed to be caused by operating the caustic feed to the scrubber at less than the theoretical amount needed to completely neutralize the acid gases in the exhaust. In April 1990, HCl emissions ranged from 21.6 lbs to 276.0 lbs per hour. In June 1990 tests, HCl emissions ranged from 12.6 lbs to 46.5 lbs per hour.
When burning halogenated organic compounds, it can also be expected that various species of dioxins and furans may be produced as products of combustion. The MSP facility has been evaluated for emissions of that family of compounds. The most toxic of those species is 2,3,7,8-tetrachlorodibenzo-p-dioxin (TCDD). To account for the toxicity of other species of dioxins and furans, the other species are expressed in what is known as toxicity equivalents of TCDD. In this manner, the total toxicity equivalent expressed as TCDD can be found. For MSP, mass emission rates per unit of time were given for the various measured species of dioxins and furans. For public health assessment purposes, it is more useful to review concentration data of pollutant species; consequently, an average effluent rate had to be assumed to determine stack concentrations of the various species of dioxins and furans. Following discussions with MSP personnel, an exhaust rate of 62,000 dry standard cubic feet per minute was used to determine the stack concentrations. The total equivalent TCDD release was calculated to range from 0.00216 micrograms per cubic meter (µg/m3) to 0.00310 µg/m3.
PAHs are a class of organic compounds that have been considered as PICs. During the stack tests conducted in 1985, four PAHs -- fluoranthene, naphthalene, phenanthrene, and pyrene -- were fed in sufficient quantity in the feed materials to allow a DRE to be calculated for the effluent gases. The calculated DRE for all four compounds exceeded 99.99%.
The discussion of air emissions associated with MSP plant activities presented in the previous paragraphs focuses on measured stack emissions. Although useful, that discussion is not complete for the following reasons:
o Stack tests are not designed to reflect on-site "fugitive air emissions," such as releases of volatile organic compounds (VOCs) produced when blending or shredding feed materials or simple process leaks of combustion gases.
One way to assess plant emissions, including fugitive emissions, is to monitor ambient air at various locations throughout the facility. The results of such monitoring could reflect stack downwash emissions (under certain atmospheric conditions), emissions of VOCs associated with handling, blending, or storage of hazardous materials, and background levels of pollutants migrating onto MSP property.
Some ambient air monitoring has been conducted at MSP. One source of ambient air quality data is MSP's industrial hygiene data used to monitor the quality of workers' breathing air at various facility locations. Another source of data is the four-station ambient air monitoring network maintained by MSP at the site perimeter. In addition, EPA has conducted on-site and off-site ambient air monitoring. Data reviewed by ATSDR from those sources was generated between 1987 and the first quarter of 1990.
Parameters monitored in the ambient air include dichloromethane, chloroform, 1,1,1-trichloroethane, trichloroethylene, benzene, tetrachloroethylene, 1,2-dichloroethane, carbon tetrachloride, toluene, and trichlorofluoromethane. Much of the data reported by MSP is expressed in terms threshold limit values (TLVs). TLVs are used to measure occupational exposures to airborne concentrations of substances. They represent the conditions under which it is believed that nearly all workers may be repeatedly exposed to a substance without sustaining adverse effects. Some of the data are expressed as actual concentrations of pollutant per unit volume of air (e.g., µg/m3).
In general, the overwhelming majority of data reviewed suggests that levels of organic vapors emitted on site, at least for the monitored substances(1), are less than levels of concern for occupational or off-site public health exposure. For example, of the nearly 2,000 data points for all of 1989 workplace air data (MSP), only one data point exceeded the TLV for dichloromethane near stockpiled product; a few approached the TLV for carbon tetrachloride near the drum process area. Most of the on-site samples, including EPA's sampling, are less than TLV/42 or TLV/100, which are values sometimes used by state or local air pollution agencies to assess public exposures to such compounds (R-66). The divisor of 42 or 100 is used to adjust for residential exposure, which may be continuous, versus occupational exposure, which is limited to about 40 hours per week. No other standards exist. It should be noted that this discussion focuses on on-site levels, and it is expected that dispersion would further reduce off-site concentration levels, if there are no other off-site contributions of the same species of pollutant.
There have been citizen allegations of heavy smoke releases from the MSP operation, particularly during first couple of years of operations at the facility. It is difficult to assess the impact of those reports because they were not quantified or characterized. It is assumed, however, that the current ambient air network monitoring results reflect current conditions, including any combustion problems that could result in heavy smoke releases at times when the smoke would circulate to the ground near the stack.
Water: On-site water contamination could exist in surface waters, such as stormwater runoff that contacts stored product, feed materials, or potentially contaminated site soils. Rainwater percolating through product, feed, or surface soils downward into underlying groundwater also could be a source of on-site water contamination. LDEQ inspection reports cite a number of on-site material storage conditions that could lead to such water and soil contamination. To assess on-site water contamination, environmental regulatory agencies and MSP have undertaken several sampling and monitoring activities.
The results of surface water sampling by the state in 1986 showed no lead, phenols, cyanides, chlorinated hydrocarbons (including pesticides), polychlorinated biphenyls, phthalates, or nitroaromatics. Zinc and copper were detected at less than part per million (ppm) levels. No details were provided about exact sample conditions or locations.
In July 1989, EPA conducted substantial environmental tests both on and off site. In addition to
air, soil, and sediment, EPA tested on-site monitoring and test wells for groundwater
contamination. Barium ranged from below detection levels to a high of 1,830 parts per billion
(ppb). Arsenic ranged from none detected to a high of 987 ppb (D-48a). A partial list of organic
species detected are shown in Table 3.
| Table 3 | |
| On-site Groundwater Contamination (Partial List) | |
| Compound | Maximum Detected |
| Polynuclear Aromatic Hydrocarbons | 26 ppb |
| Pentachlorophenol | 144 ppb |
| Trichlorophenol | 47 ppb |
| 4-Methylphenol | 2210 ppb |
| Di-n-butylphthalate | 6 ppb |
| Reference: D-28 | |
In 1987, MSP monitored on-site groundwater and found naphthalene, phenol, and phenolic compounds in the vicinity of the well designated MW-4 (D-115). In response to that finding, a Remedial Action Plan (RAP) was begun to address the contamination and to assess the physical extent of the contaminated groundwater plume. Several additional on-site monitoring wells were added in 1988. Data collected by MSP in 1988 and 1989 suggest that the contaminated plume remains, although the phenol and phenolic compounds were reduced by about 30% in a one-year period (D-127). In other on-site monitoring wells (Resource Conservation and Recovery Act (RCRA) and non-RAP wells) no hazardous substance list (HSL) compounds were found, except for methyl chloride and bis(2-ethylhexyl)phthalate, both of which may be artifacts (both are commonly associated with plastic pipe well construction). Metals, including lead, chromium, and cadmium were found in RCRA monitoring wells in below-parts-per-million range, in 1988 (D-107a). EPA findings for these metals in 1986 groundwater monitoring well data were in some cases somewhat higher than the MSP sponsored data, however, the maximum values were still under one part per million for all three metals mentioned here (D-48a).
SOILS, SEDIMENTS, AND AGGREGATE: On-site soils and sediments can be contaminated when feed materials or process residuals are stored in a way that allows rain water to leach through solid materials into the underlying soils. Liquid feed materials or spills or leaks can percolate directly into the underlying soils.
In 1989, EPA sampled on-site soils, sediment, and aggregate (D-48a). In on-site surface fill areas, lead ranged from not-detectable up to 454 ppm (TCLP). Cadmium in those areas was as high as 4.8 ppm (TCLP). Total lead and cadmium soil concentrations were up to an order of magnitude higher than the leachable (TCLP) values. Some fill areas showed no or virtually no volatile organic or semi-volatile chemical contamination. Other fill areas were contaminated with PAHs in the 2 - 10 ppm range. Dibenzofuran in the fill areas ranged from 321 ppb to 755 ppb. Piles of aggregate sampled on site contained total lead ranging from not detectable to 5590 ppm and total cadmium ranging from not detectable to 41.8 ppm. The piles showed virtually no volatile or semi-volatile organic chemical contamination.
The 1987 U.S. Coast Guard on-site soil study did not show lead or cadmium in soils at levels exceeding EPA leaching (Extraction Procedure Toxicity) criteria. Those criteria estimate the amounts of metals released from the soil and available for absorption if exposure occurs. The maximum lead and cadmium levels found in that study of on-site soils were 8,363 ppm and 51,442 ppm, respectively. Leachable levels were much lower.
Aggregates stored on site include primary kiln aggregates, which are solids discharged from the rotary kiln with only the shredded metal drums removed, and slagged aggregates, which are solid materials resulting from further heating and slagging primary aggregate and solids captured by the air pollution control system (e.g., baghouse dust). Primary aggregate that exceeds 80% of the allowable TCLP criteria for any metal is treated in the slagging kiln. MSP reports that slagged aggregate must pass TCLP criteria to be sold. For this public health assessment, ATSDR reviewed "Comprehensive Analytical Results for MSP Aggregates -- 1989," an MSP report on analytical results of primary aggregate, slagged aggregate, and baghouse dust. For lead, a primary pollutant of concern, the maximum reported contamination levels in baghouse dust were 29,796 ppm total lead versus 438.6 ppm leachable lead (TCLP). For primary aggregate, the maximum reported leachable lead level was 131.21 ppm (TCLP). For slagged aggregate, the maximum reported leachable lead was 16.21 ppm (TCLP); that was the only data point for slagged aggregate that exceeded the TCLP criterion of 5.0 ppm for lead. Ninety-two percent of the data points reviewed by ATSDR for slagged aggregate showed leachable lead under 0.05 ppm. A few data points were between 0.5 ppm and 5.0 ppm for leachable lead. It should be noted that those are data reported by MSP to be used for internal quality assurance to determine which aggregate can be sold and which must be further processed.
B. OFF-SITE CONTAMINATION
As mentioned in the preceding section, with the exception of in situ soils, any contaminated media originating on site at the MSP facility could migrate off site. These contaminants could include airborne particulates and gases and waterborne substances in groundwater or surface water. Also, process residue or aggregate destined for off-site use could be a source of contamination if the contaminants are in a biologically or environmentally available form. This section reviews the available characterization data regarding off-site contamination. As in the preceding section, data are reviewed for extreme values. A notable difficulty in evaluating off-site data is the confounding nature of other pollution sources in the area, such as automobile emissions, other industrial activities, and old waste disposal sites. A review of the 1987 and 1988 Toxic Release Inventory (TRI) confirmed that there are other industrial chemical releases in the area, which are considered in this public health assessment.
Air: Off-site ambient air monitoring data are rather limited and are particularly difficult to link to MSP because of other potential area sources of emissions and the lack of clear identification of "signature compounds" that would be expected to be emitted only from MSP. The most recent large-scale study of off-site ambient air quality available for ATSDR review is the EPA monitoring conducted in August 1989. For that study, seven sampling sites were set up at the MSP facility; four more stations were located off site toward and in Amelia. A number of organic species, including 1,1,1-trichloroethane, xylenes, 2-butanone, vinyl acetate, and 2-hexanone were found at higher concentrations at the MSP site than at the off-site locations. Concentrations of those compounds at MSP were typically under 100 µg/m3 (except one point for 2-hexanone at 211 µg/m3) which is less than TLV/100 for the compounds reviewed. Cadmium and lead were also measured; there were virtually no differences in lead and cadmium values found at MSP and off site. Lead ranged in concentration from 0.17 µg/m3 to 0.20 µg/m3 on site and from 0.18 µg/m3 to 0.19 µg/m3 off site. Cadmium ranged in concentration from 0.0013 µg/m3 to 0.0090 µg/m3 on site and 0.0077 µg/m3 to 0.0084 µg/m3 off site. Meteorologic data were not available for ATSDR review; consequently, upwind/downwind comparisons could not be made.
Water: Off-site water contamination could originate from contaminated surface water runoff from a site, movement of contaminated groundwater off site, spills or leaks to adjacent sites, and discharges to adjacent receiving waters. All of those mechanisms for off-site water contamination have been reported or alleged regarding MSP site activities. LDEQ site inspection reports and EPA studies reviewed site conditions and on-site and off-site waters to evaluate the potential for off-site water contamination. The other potential for off-site water contamination associated with MSP activity is the leachability of contamination (lead and cadmium) from the aggregate.
In July 1989, samples were taken from water in the adjacent Bayou Boeuf and from site
discharge outfall points as part of the EPA RCRA inspection. No lead or cadmium was detected
in the bayou water samples. Outfall number 3 showed no lead or cadmium and 89 ppb barium.
Outfall number 4 showed 226 ppb lead, 15 ppb cadmium, and 443 ppb barium. Most of the
off-site water samples, including two field blanks contained 2 - 5 ppb of di-n-butylphthalate.
Outfall number 4 also showed 3.6 ppb chloroform contamination.
| Table 4 | |||
| Other maximum value outfall discharge data | |||
| Substance | Concentration | Outfall | Date Sampled |
| 1,1-dichloroethane | 29 ppb | 4 | 12/12/89 |
| chlorobenzene | 18 ppb | 1 | 12/06/89 |
| chloroform | 2.5 ppb | 1, 3 | 12/06/89 |
| isophorone | 47.3 ppb | 1 | 12/12/89 |
| phenol | 71.4 ppb | 3 | 12/12/89 |
| naphthalene | 34.2 ppb | 3 | 12/12/89 |
| 1,1,1-trichloroethane | 119 ppb | 4 | 12/12/89 |
| carbon tetrachloride | 21 ppb | 4 | 01/20/90 |
| lead | 22 ppm | 1 | 03/01/90 |
| cadmium | 1.6 ppm | 1 | 03/01/90 |
| toluene | 17 ppb | 1 | 03/07/90 |
| Reference: D-126 | |||
As mentioned previously, contaminated groundwater beneath the site could migrate off site. In 1989, Woodward-Clyde Consultants prepared a groundwater investigation report for MSP. The report stated that groundwater beneath MSP persistently "trends" toward Bayou Boeuf, based upon observations in 1988 and 1989. On-site groundwater quality is described in the On-site contamination section. Off-site groundwater quality is more difficult to characterize in this case, because it is believed that site groundwater discharges into Bayou Boeuf, a surface water.
Soils, Sediments, and Aggregate: The greatest off-site contamination potential for those solid media would be expected to be associated with placing aggregate on soils in support of new construction, roads, and parking lots. Sediment contamination would be expected in bayou sediments adjacent to the MSP storage, handling, and processing area. Table 5 summarizes the highest values of the data reviewed for in-situ aggregate lead and cadmium contents. Those data, assembled in 1989, are for aggregate, possibly mixed with some soil, at six off-site locations. People could be exposed to off-site aggregate by inhaling fine, airborne particles or by ingestion (particularly in children). Ingestion of significant amounts of aggregate that has been slagged would not be expected because of its generally coarse structure. (See Public Health Implications section.)
| Table 5 | ||||
| Off-site soil/aggregate lead and cadmium results High Values Found (parts per million) | ||||
| Area Sampled | Total | EPTox* | ||
| Lead | Cadmium | Lead | Cadmium | |
| Amelia Community Center
Background |
1,140 ND |
22 ND |
ND ND |
ND ND |
| Berry Brothers Background |
12,800 ND |
ND ND |
ND ND |
ND ND |
| Cypress Gardens Subdivision Background |
1,920 ND |
19 ND |
ND ND |
ND ND |
| Residence (aggregate used under house) Background (neighbor) |
1,110| 15 |
ND ND |
ND 0.07 | ND |
| Lowlands Construction Background |
3,860 43 |
39 ND |
1.0 ND |
ND ND |
| Ranch (aggregate used in driveway) Background |
2,580 ND |
16 ND |
ND ND |
ND ND |
| ND -- not detected
* -- Extraction Procedure Toxicity - test to determine the amounts of contaminants that will leach under environmental acidity conditions Reference: D-28 | ||||
Other contaminants found at the Amelia Community Center included arsenic at 32 ppm (versus 3.8 ppm background); barium at 26,300 ppm (versus 248 ppm background); and chromium 192 ppm (versus 25 ppm background). Mercury was not found in either the aggregate or the background samples.
Generally, volatile organic and semi-volatile organic compounds were not found in the samples. One sample at the Berry Brothers site contained 0.522 ppm of a phthalate compound. Several samples in the Cypress Gardens subdivision contained ppm-range chlordane, and one sample at an aggregate-contaminated fenceline contained 1.20 ppm hexachlorobiphenyl.
Sediments and bottom bayou soils near the MSP facility have also been analyzed over the life of MSP operations. After one alleged spill in 1986, chromium in sediment was reported by LDEQ to range from 51.1 ppm to 91.2 ppm (dry). Later that same year, downstream sediment was reported to contain 8.33 ppm chromium; sediment at the plant contained 10.33 ppm chromium. In 1988, LDEQ reported that sediment samples taken near a storage barge that allegedly leaked coal tar creosote wastes contained organic contaminants characteristic of those materials and in a proportion consistent with the wastes. In 1989, EPA further sampled Bayou Boeuf bottom soils; following are the results:
| Table 6 - Sediment Samples from Bayou Boeuf | |
| Total Lead | 53 to 20,900 ppm |
| Total Cadmium | not detectable to 351 ppm |
| Barium | 3,350 to 26,400 ppm |
| Arsenic | up to 115 ppm |
| PAHs | up to 20 ppm |
| Reference: EPA RCRA Inspection, July 1989 | |
Few background sediment data were available for evaluation. In 1976, the U.S. Army Corps of Engineers analyzed Bayou Boeuf sediments sampled 0.5 mile below Highway 90 near Amelia. That part of the Bayou is not in an industrial area. Results showed comparatively low metals levels, but high levels of organic compounds and low-level polychlorinated biphenyl (PCB) contamination.
Food Chain Data: In addition to potential contamination of off-site media, contaminants from a site such as MSP could bioaccumulate in various plants and animals eaten by people. There appears to be little possibility that site contaminants would affect edible plants because of the lack of agriculture near the facility. Local residents are concerned, however, about possible impact on peaches and pecans grown near soils where aggregate has been placed. ATSDR has no data on potential contamination of peaches and pecans; that topic will be discussed further in the Pathways section of this public health assessment.
Limited data are available on the flesh quality of fish caught near MSP. In 1986, mercury and barium contamination (0.625 ppm to 1.0972 ppm and 2 ppm to 11.4 ppm, respectively) were found in edible parts of fish caught about 75 yards southeast of MSP (D-149). In fish studies by LDEQ in 1987 (see table) there were no remarkable differences between the edible portions of catfish and carp found in Bayou Boeuf near MSP and in the same bayou about one fourth mile south of Lake Palourde.
| Table 7 - FISH DATA - 1987 | ||
| Near MSP | Near Lake Palourde | |
| p,p' - DDE | ND to 0.013 ppm | 0.018 ppm |
| Arochlor 1254 (PCB) | ND to 0.10 ppm | 0.14 ppm |
| Pentachloroanisole | ND to 0.004 ppm | 0.002 ppm |
| Metals | Not reported | Not Reported |
| Reference: D-63 | ||
In 1989, LDEQ again analyzed for various organic compounds in edible portions of fish caught near MSP; no analysis for metals was conducted. Most results were nondetectable or below-detection levels. The following table summarizes the maximum contaminant levels detected:
| Table 8 - Fish Data - 1989 | |
| butyl benzyl phthalate | 2.040 ppm |
| 1,2,3,5-tetrachlorobenzene | 0.0676 ppm |
| 1,2,4,5-tetrachlorobenzene | 0.0676 ppm |
| 1,2,3,4-tetrachlorobenzene | 0.0503 ppm |
| 1,2,4-trichlorobenzene | 0.035 ppm |
| Reference: D-70 | |
The available fish data do not address shellfish which are an important source of food in the region.
C. QUALITY ASSURANCE AND QUALITY CONTROL
This public health assessment is based largely on data developed by LDEQ, EPA, and MSP. When QA/QC measures were described, they appeared consistent with measures normally taken during environmental sampling and analysis. All data were considered as received, regardless of whether a QA/QC description was included; however, ATSDR recognizes that QA/QC procedures and sampling and analysis methods may not be uniform for all data received. All ATSDR-gathered data sources are listed at the end of this document.
D. PHYSICAL AND OTHER HAZARDS
The MSP facility is an active industrial operation with the same potential for accidents that would be expected at any similar facility. There is clear evidence of an ongoing worker safety program. The facility is fenced to discourage unauthorized entry; access to the active processing area is through a guarded weighing station.
A. ENVIRONMENTAL PATHWAYS (FATE AND TRANSPORT)
Air: Contaminated air originating at the MSP site from either fugitive storage, handling and process emissions, or as stack emissions disperses to surrounding air depending on local meteorologic conditions. Effective stack height and exhaust velocity also significantly influence the dispersion characteristics of stack emissions. To assess the significance of site air emissions, ATSDR must review the hazard properties of each contaminant, note the typical and maximum concentration levels, and evaluate the locations of potentially exposed people with respect to source emissions. Wind direction and speed and natural dilution, decay, or contaminant transformation mechanisms also affect human exposure levels.
From the data reviewed which measured on-site and off-site air contamination, the indicators of ambient air quality (i.e., MSP's industrial hygiene data and ambient air data, and EPA's ambient air data) do not show cause for concern that the health of neighboring communities is being affected. That observation is based on the overwhelming number of data points showing that chemical contamination on or near MSP operations is well under TLVs established for the species observed (i.e., less than TLV/42, TLV/100, or even TLV/1,000). Given the natural dilution of such contamination as the air moves away from the facility, and the presence of other sources of similar pollutants in the area (as reported in the TRI data for the area in 1987 and 1988) it may not be possible to detect specific pollutant increases from MSP, especially at distances to the nearest major populations. Anecdotal reports indicate that winds are predominantly out of the north, which would tend to carry air pollutants in the direction of the Bayou Boeuf, which is uninhabited. Unfortunately, no local long-term windrose was available to confirm or refute that observation. A one year general wind direction observation at the facility, however, showed that winds tend to blow airborne pollutants away from populated areas about two thirds of the year.
Stack emissions likewise follow the predominant wind direction; however, local terrain coupled with effective stack height and exit gas velocity can result in variation of ground- and stack-level emissions. In the next section, Human Exposure Pathways, a number of types of stack emissions will be evaluated to determine their significance to human health.
In general, no ongoing real-time or averaging off-site air monitors are in the area that could be used to assess short- or long-term air emissions from MSP to the nearest populations. Although it might be very difficult to establish monitoring systems that would not be confounded by other air emissions in the area, such systems could help detect a massive release, such as might occur if a waste tank truck overturned and ruptured while entering the facility. Also, if data were collected over a sufficient time period and in conjunction with local meteorologic data, additional information might support or refute the hypothesis that it may not be possible to measure MSP's impact on air in residential areas away from the plant.
Water: Contaminated groundwater and surface water originating at the site and discharges from site outfalls all empty into Bayou Boeuf. The bayou generally flows toward the Gulf of Mexico; one citizen stated, however, that under certain tidal conditions the bayou flows up to Lake Palourde, which is a source of potable water for the local communities.
The other potential off-site water pollution pathway involves the leach potential of the aggregate in the natural environment. MSP quality assurance data reported that the aggregate passes EPA's leaching test criteria and consequently should not leach to other ground or surface waters. The community expressed skepticism about the appropriateness of the EPA leach tests for assessing bioavailability of lead or cadmium in aggregate that might be ingested. That issue will be discussed further in the Toxicological Implications section of this public health assessment.
Soils, Sediments, and Aggregate: Contaminated site soils at MSP are not likely to migrate off site, particularly if left undisturbed. Since operations began in 1985, part of the site has been paved to improve storage and containment capacity. Windblown soil particles from the site would be expected to "fall out" locally and not affect neighboring communities. Sediments in the adjacent bayou might or might not migrate substantially. Factors influencing such migration could include major storms that affect tidal flow and deposite new contaminated or uncontaminated sediments that cover and immobilize existing sediments.
Off-site aggregates can be applied or stored where children and adults have direct access to the aggregate; fine particles can become windborne and transported by air. Once aggregate is applied and covered with asphalt, as in a paved road or parking lot, it is assumed that contaminants are relatively immobile, except for relatively slow releases following abrasion and wear.
Food Chain: There are conflicting reports about the consumption of fish from surface waters near MSP. MSP and LDHH report that Bayou Boeuf is heavily traversed and, consequently, little sport or commercial fishing takes place near MSP. The community, however, says that there is a significant amount of fishing in local waters. The food chain pathway is difficult to evaluate because of the limited data available and the confounding effect of other pollution sources in the area that could affect water and fish quality. Also, the available data, which are limited, suggest there is no significant difference in the quality of fish examined from Bayou Boeuf and those from Lake Palourde. See the Human Exposure Pathways and the Public Health Implications sections of this public health assessment for further discussion of that topic.
Limited data are available to evaluate the possible migration of aggregate contaminants into nearby crops, such as the peaches or pecans. In the absence of data, such as the assay of pecan meats or peach flesh, ATSDR must base its analysis on the known characteristics of the aggregate and the growing sites in question.
Regarding the aggregate, it has been shown that contamination from organic compounds is largely nonexistent, as would be expected following combustion. It has also been shown that total metals, such as lead and cadmium, can be quite high; on the other hand, leachable metals including lead and cadmium as assayed by EP toxicity or the TCLP tests are low.
The following observations were made about the specific sites where aggregate has been deposited. The aggregate was placed as fill along a fenceline dividing three properties. Some of the aggregate spilled or washed across the fenceline into two neighboring properties. Mature, productive peach and pecan trees are in two yards adjacent to areas where the aggregate is reported to have migrated. ATSDR does not know if the roots of those trees extend into soils where the aggregate migrated. Using available information, however, it is not likely that either the peaches or pecans would sustain measurable contamination from metals in the aggregate. Water percolating through the soil/aggregate mix is not likely to be a stronger leaching agent than acid used in the EPA leaching tests; consequently, the metals should remain bound in the aggregate matrix. Assays of the peaches and pecans would help to resolve that issue.
B. Human Exposure Pathways
Air: In the preceding section of this document, a discussion of ambient air releases concluded that there would not be significant or incremental exposure to fugitive plant emissions by citizens in neighboring communities. That conclusion was based on the low measured concentrations of organic species near plant operations. Also, limited meteorologic data indicate that such emissions would tend to move away from populated areas. A small number of MSP employees live in mobile homes immediately west of the active facility. Again, the reported data, coupled with the apparent prevailing wind information, suggest that even that population would not inhale fugitive emissions at levels of health concern.
Many stack emissions data are reported in terms of pounds of pollutant emitted per hour. To evaluate potential human exposure, that information must be translated into potential exposure concentration levels. As a part of this public health assessment, ATSDR conducted two screening exercises. First, using the reported volumetric flow rate of stack effluent, pollutant concentrations were determined. Stack concentrations approached or exceeded TLV were then analyzed with a mathematical air dispersion model based on worst-case assumptions to determine maximum ground-level concentrations (MGLCs) of any species of concern (R-76). MGLCs were then reviewed with respect to possible impact on public health. Generally, no environmental standards exist for human exposure by way of inhalation to many of the pollutants reviewed in this manner. This approach is crude and serves only as a screening tool to estimate order-of-magnitude concentrations and thereby indicate situations that merit closer examination. ATSDR policy stipulates that modeling cannot serve as a proxy for actual measurements of existing conditions when public health implications are being determined.
Using a stack gas flow rate of 62,000 dry standard cubic feet per minute, three of seven metals (chromium, mercury, and nickel) exceeded the lowest TLVs for the most toxic species of the parent metals. After calculation of MGLCs, nickel and chromium were found to be about 1/160th and 1/80th of their TLVs, respectively; mercury was about 1/8,000th of its TLV. In the absence of standards for that type of exposure, some regulatory jurisdictions have used 1/42nd, 1/100th or 1/1,000th of the TLV as a criterion for acceptability of an emission (R-66). For this analysis, nickel and chromium are the metals of concern, and the State of Louisiana has identified those two metals as being emitted in excess from the incinerator stack (state stack test announcement in 1988). The state's use of a more refined model than that used by ATSDR resulted in it finding slightly lower concentrations than ATSDR. The general orders of magnitude, however, were in close agreement. The state-generated data also showed that MGLCs for nickel and chromium were under TLV/42. Maximum chromium and nickel emissions in June 1990 were more than 100 times lower than the maximum values used for this screening exercise.
The method used by ATSDR to calculate MGLCs for metals resulted in an approximate
10,000-to-1 dilution ratio of the stack gas concentrations. The state's model dilution factor was
about 30% greater (13,000 to 1). For the remainder of this analysis, the more conservative
(worst-case) ATSDR factor will be used to estimate MGLCs for other pollutants from the stack
(Table 9). Use of the lower dilution factor results in a higher exposure estimate.
| Table 9 | ||
| Selected High-Value Stack Emission MGLC Estimates | ||
| Compounds | Stack Concentrations | Estimated MGCL |
| Dioxins | 0.0031 µg/m3 | 0.00000031 µg/m3 |
| Carbon Monoxide | 136,842 µg/m3 | 13.68 µg/m3 |
| 1,1,1-Trichloroethane | 2461 µg/m3 | 0.25 µg/m3 |
| Trichloroethylene | 1181 µg/m3 | 0.12 µg/m3 |
| Sulfur Dioxide | 64,650 µg/m3 | 6.46 µg/m3 |
| Hydrogen Chloride | 1,793 mg/m3 | 179.3 µg/m3 |
| Nitrogen Oxides | 180 mg/m3 | 18 µg/m3 |
| Reference: D-100, D-137 | ||
The preceding discussion and estimates are used to screen for possible human exposures of public health concern. It must be remembered that they are based on highest reported emission levels and a meteorologic scenario that yields the highest ground-level concentrations of a pollutant. Even with that bias, most pollutants are well below levels of health concern. For example, are below TLV/1000 for worst-case maximum concentrations. HCl is the only species that exceeded TLV/100 in this exercise (179 µg/m3 versus 75 µg/m3). Actual average human exposures are likely to be considerably less than the modeled values. Values for the pollutants carbon monoxide, sulfur dioxide, and nitrogen oxides did not exceed National Ambient Air Quality Standards.
Water: Considering the available data, human exposure to water contamination associated with MSP activities and produced aggregate should be inconsequential. Surface water and groundwater from the site flow into Bayou Boeuf, where they could have a localized impact on water quality. With the considerable dilutional capacity of that body of water, however, ATSDR estimates that the current pollution load is not likely to be detectable above background levels within several hundred yards from the discharge point. Past alleged discharges may have had more lasting effects on bayou sediments, which could in turn contaminate the waters above. However, with the normal flow of the bayou toward the Gulf of Mexico (away from the drinking water intake), and the distance and dilution that would be experienced during unusual tidal events (when water would reverse its normal flow away from the Gulf) it is highly unlikely that drinking water from Lake Palourde would be significantly affected by this source.
Under normal conditions, aggregate has not been shown to leach significantly, particularly when assessed using the EPA leachability tests, which should be appropriate for environmental pH conditions. Consequently, water percolating through the aggregate in situ (in its position) should not create the possibility of human exposure to site contaminants when water is ingested.
Soils, Sediments, and Aggregate: Human exposure to contaminated MSP soils or nearby sediments is not expected to be a public health problem. Levels of soil contamination on site are low, and the site is not particularly convenient as a play area. Similarly, sediments in the bayou are not normally easily accessed by humans.
Human exposure to aggregate is possible when the aggregate is applied to a surface, but not paved over or otherwise covered. Possible routes of exposure include inhalation, ingestion of windblown aggregate particles, and direct ingestion of aggregate by children playing in or on exposed aggregate. The significance of this route of exposure is discussed in the Public Health Implications section of this public health assessment.
Food Chain: A potential for human exposure to contaminated fish, and/or peaches and pecans has been identified. Data were too limited to determine potential sources of fish contamination; however, in general, there does not appear to be a fish contamination problem clearly attributable to MSP. One fish sample in 1986 had mercury levels of possible public health concern; however, the contamination was not shown to be linked to MSP activities or site contaminants. Regardless of the source of contamination, it would be wise to perform additional fish assays for metals contamination to better understand whether that one fish sample was representative of local fish populations. Subsequent fish assays focused on organic contaminants rather than metals.
ATSDR is not aware of any assay data for the peaches or pecans discussed previously in this report; consequently, human exposure potential from the food chain cannot be addressed. It is recommended that those foods be assayed for metals, particularly lead and cadmium, to resolve concerns of the owners of the potentially affected trees.
A. Toxicological Implications
Air: Evaluation of data and pathways did not indicate a potential for people to be exposed to levels of health concern. Under worst-case conditions in the modeling, nickel and chromium may be emitted from the stack at levels above health comparison values. Nickel is a silvery metal that occurs naturally in the environment. People can be exposed to nickel compounds by way of inhalation, ingestion of food or water containing nickel compounds, and/or skin contact with many consumer products (R-11). Nickel exposure by inhalation is small compared to the amount consumed in the average diet. Insoluble nickel compounds that are inhaled can accumulate in the nasal mucosa and lungs, depending on the size of the particles. Tobacco smoke contains relatively high levels of nickel compounds, including nickel carbonyl. About 5% of people are sensitive to nickel; the most common adverse effect is skin sensitivity (R-4). Individuals not sensitive to nickel have not been shown to have adverse effects from long-term exposure by inhalation (R-4). Using a worst-case scenario, ATSDR considers the nickel levels potentially emitted from the facility to be below those of health concern.
Chromium is an element found in three valence states in the environment: chromium(0), chromium(III), and chromium(VI). Chromium(III) occurs naturally; the others are produced by industrial processes. Chromium(III) is believed to be an essential element for the body's use of glucose. Chromium compounds are used in chrome plating, and as catalysts in steel and other alloy production, leather tanning, wood and water treatment, and photography (R-68). Human exposure could result by way of food intake and, to a lesser degree, by way of dust inhalation and water ingestion. People are usually exposed by inhaling the metal and its salts. Insoluble chromium compounds are deposited in the lung (R-11). Long-term exposure to chromium(VI) has been found to cause cancer in animals. Exposure to high levels of chromium by way of inhalation has been associated with lung cancer in workers (R-3). Levels found at the site are below recommended health guidelines and should not pose a public health risk.
Hydrogen chloride (HCl), a colorless, water-soluble gas, was also potentially emitted at moderate levels from the plant when a worst-case scenario was used. In aqueous solution, HCl is known as hydrochloric acid or muriatic acid; it can be corrosive to the skin, eyes, mucous membranes, and respiratory tract. People with skin, respiratory, or digestive diseases can be more sensitive to the effects of HCl(R-29). Irritation can occur at exposure levels above 5 ppm. Worst-case ground-level concentrations from MSP activities were found to be less than 1 ppm. No significant effects have been seen following chronic exposure to low levels of the gaseous form of HCl (R-63, R-80).
Water: Past spills of aggregate into a localized area of the bayou raise questions about the leachability of lead and cadmium into surface water. Leachability testing at environmental pH indicates that the spills should not be a problem under normal environmental situations. EPA tests of surface waters in the area did not find significant levels of lead or cadmium. Therefore, their presence is not believed to be of public health concern.
Barium was found in the water of Bayou Boeuf at levels ranging from non detectable to 1830 ppb. In its National Interim Primary Drinking Water Regulations, EPA set its allowable concentration of barium in domestic water supplies at 1000 ppb (R-11). Those regulations apply only to community drinking water systems. In May 1989, the Proposed Maximum Contaminant Level (PMCL) for barium, 5000 ppb, was published in the Federal Register. The barium in Bayou Boeuf is below levels that pose a threat to public health.
Soils, Sediments, and Aggregate: There is community concern about past discharge of creosote from a storage barge into the bayou. Creosote is a heavy, oily, colorless liquid that has a characteristic smoky, tarry odor. If contaminants are present creosote is a brown to black color (R-68). Creosote is essentially insoluble in water. The primary route of human exposure at MSP, therefore, would have been by direct dermal contact and , possibly, exposure by inhalation of creosote stored on the barges. Ingestion of the water from the bayou would not have been an exposure route. Creosote is a varied mixture consisting of about 85% PAHs and 2 - 17% phenolic compounds. PAHs from creosote released into surface water tend to bind to soils and sediment particulates with low solubility and mobility. PAHs have been found in surface waters throughout the United States; concentrations in sediments are generally much higher than in surface waters. Creosote irritates the skin; long-term exposure to low levels can cause reddening, blistering, or peeling. Dermal exposure was a possible route of exposure for workers on the barges and for workers around the barge area when the barges were present. Following removal of the barges, and given the limited access to Bayou sediment, human exposure to creosote in sediments is not likely (R-7).
Two issues have been raised about the safety of the aggregate: leachability of metals from the matrix and the fibrogenic potential (the ability to form a protein clot in the lungs) of small particles of the material. The metals of primary concern are cadmium and lead. Children are more sensitive than adults to effects of lead exposure. The central nervous system is the primary target organ for lead toxicity in children (R-50, R-16, R-49, R-58, R-23). Recent studies indicate that adverse effects on the function of the central nervous system persist into adulthood (R-51). New data also indicate significant adverse effects in children with blood lead levels previously believed to be safe. Current information has shown disturbances in neurobehavioral development in children with blood lead levels in the range of 10 - 25 µg/dL and in children whose mothers had blood lead levels in that range during pregnancy. There has been some indication that effects occur at blood lead levels below 10 µg/dL (R-9). The Centers for Disease Control has recently recommended that the intervention level be established at 10 µg/dl (R-84). The earliest intervention is health care workers counseling of parents and identifying possible sources of lead exposure for children. Lead has been shown to leach from soils, and blood lead levels in children appear to be related to the level of contamination in their environment (R-28). Blood lead levels generally rise 3 - 7 µg/dL for every 1,000 ppm increase in soil or dust concentrations (R-84). Experimental studies relating blood lead levels to dietary lead intake for adults produced estimates of a 0.02 µg/dL increase in blood lead per microgram of lead per day of total intake (R-8).
Laboratory results on the aggregate at one residence suggested that the leachable lead concentration was 7 µg/gm. The slagged aggregate cannot be directly compared to soil because the particle structure might bind the materials in a manner similar to pottery glazes (i.e., leaching of lead from the aggregate may be similar to lead glazes in ceramic material rather than leaching of lead from soils). The amount of lead leached from ceramic material varies with the percent of lead in the glaze, the other constituents (pigments), and the temperature of the firing (R-27, R-57).
The aggregate produced at MSP contains a high level of lead. However, the firing temperature might be high enough to reduce leaching. EP Toxicity and TCLP testing did not indicate significant leaching of lead at environmental pH. Further study done at a pH of 1 indicated increased amounts of leaching. A pH of 1 is closer to the pH of the stomach and could indicate leaching potential from ingested aggregate. Digestion in the stomach is initiated by release of HCl. Distention of the stomach by food triggers the release of gastrin, a hormone that controls production of HCl in the stomach. A gastric pH of 3.0 begins to inhibit gastrin production; production ceases at a pH of 1.5. When gastrin production stops, HCl production also slows. The average pH reached in the stomach is 1.4. The results of leaching at pH 1 might indicate possible exposure if significant amounts of aggregate are ingested. In addition, a bioavailability study in mice showed a rise in blood lead levels after gavage feeding of the aggregate. The levels reached would not pose an acute problem; however, body burden was not examined in the study. Those data indicate that the aggregate is bioavailable to some extent at a gastric pH (D-137A); therefore, the possibility of increased body burden of lead from chronic exposure is of concern.
The normal maximum soil ingestion rate in children is estimated at 0.5 gram/day. A study using tracer elements to identify actual ingestion found a median intake of soil, in children one-year to four-years old, ranged from 0.009-0.096 gram/day. The majority had a median intake of less than 0.05 gram/day (R-18).
The average amount of soil ingested by children does not indicate the likelihood of significant acute exposure to lead by aggregate ingestion. Also, slagged aggregate is a coarse ceramic-like material, which would not be likely to be ingested in large amounts. In addition, the metals content of the aggregate varies widely. Therefore, it is not possible to determine the typical bioavailability of lead from the entire range of aggregate produced. Analysis of blood lead levels in children at a residence where aggregate was placed as foundation material did not indicate increased lead levels; however, the blood lead in one of the children was 8 µg/dL. Aggregate at the residence was "primary" aggregate and has different properties than slagged aggregate. ATSDR reviewed information on the exposure potential at this residence and data about the characteristics of aggregate at the residence. ATSDR concluded that aggregate at the residence is of potential public health concern because there is a potential for lead exposure and there is no defined threshold for chronic lead toxicity (D-24A). The aggregate at the Amelia Community Center is located under a concrete slab, which provides an effective barrier to human contact; thus, there should be no significant exposure at the community center.
The amount of cadmium in the aggregate may be of concern if a significant part of the aggregate is ingested. The kidney is the primary target organ for cadmium in people (R-77, R-67). Inhalation of cadmium has been associated with increased risk of lung cancer. Smoking is a significant source of cadmium (R-5). Only about 1 - 5% of ingested cadmium is absorbed into the body. Long-term intake of 0.005 mg/kg/day (0.075 mg/day for a 15-kg child) is not believed to pose a risk for tissue damage (R-5). Leachability information indicates that a child would have to ingest 25 grams of the aggregate daily to absorb 0.075mg of cadmium. As noted previously, the nature of slagged aggregate makes this level of ingestion unlikely for that particular material.
Use of the aggregate on roadways and other areas where crushing and dust generation are likely raises the issue of particle-induced pulmonary (affecting the lungs) toxicity. Numerous types of particles have been shown to induce lung disease (R-36, R-62, R-71). Particles with an aerodynamically equivalent diameter of less than 3.5 micrometers can be deposited in the airspaces of the lung (R-34). In a study by Schneider et al, particles with irregular, angular shapes (quartz, volcano ash, heat-treated clay) tended to produce a denser type of fibrosis (overgrowth of connective tissues, particularly in response to an injury) with associated destruction of the alveoli (air cell of the lung) (R-65).
Particles that have a long lung retention time and that stimulate digestive mechanisms of lung tissue are more likely to produce emphysema (R-39). Emphysema is a lung disease that results when the alveoli are destroyed and the lung loses its ability to expand and collapse, causing air to be trapped and breathing difficulties.
A scanning electron microscope study of particles from dust generated at a road where aggregate was placed indicates that respirable-sized particles are generated, some of which are angular in shape (D-21). These angular shapes that are respirable could be fibrogenic if inhaled. Further investigation of those particles is needed to determine what portion of such particles is actually from the MSP aggregate before this product can be used safely in areas where dust generation may occur.
At one site, arsenic was found at levels of 32 ppm (compared to 3.8 ppm background). Arsenic occurs naturally throughout the environment; most people are exposed to trace levels during everyday activities. Food is the major source of intake, accounting for between 25 and 50 µg/day (R-2). Sensitive individuals (adults) can experience symptoms of exposure after ingestion of 1,000 to 1,500 µg/day. The primary features of arsenic intoxication are gastrointestinal and dermatological (R-33, R-17). Human exposure to arsenic levels found at the MSP site should not pose a public health threat.
Food Chain: Mercury was detected in 1986 in one sample of fish from the bayou. Mercury occurs naturally in the environment in many forms, both organic and inorganic. The types of adverse health effects seen with exposure depend in part on the form of mercury (R-1, R-75). Inorganic mercury salts are nephrotoxic (causing injury to the kidney) and can produce acute tubular necrosis (death of kidney tubule tissue) (R-77). Methylmercury (organic) is toxic to the brain, particularly in the developing nervous system (R-23). Mercury has been shown to bioaccumulate in fish (particularly tuna and swordfish) in the organic form of methylmercury. The mercury reported in the 1986 samples of fish was at levels of 0.625 mg/kg to 1.0972 mg/kg. EPA estimates that adults could be exposed to levels of mercury up to 0.021 mg per day in food or water without harm to their health (R-1). The amount of fish with the mercury levels found in the Bayou that could be ingested before reaching 0.021 mg is 110 grams per day. The FDA Action Level for methyl mercury in edible portions of fish and shellfish is 1 ppm (mg/kg). One of the fish sampled exceeded the FDA action level for mercury. The amount of fish from the bayou ingested by people is not known, and information on analysis in samples after 1986 was not available. Further studies should be done to evaluate the significance of this finding.
The community is concerned that possible continued contamination of the bayou from past creosote spills could increase the potential for fish contamination. The major constituents of creosote are PAHs. Substances that are persistent and not able to be broken down in the organisms who take them up are concentrated in the tissues. Thus, the organisms at the top of the food chain (humans, carnivores) will receive the highest concentrations of these substances. This process is called food chain biomagnification. Uptake of PAHs by aquatic organisms has been demonstrated. These compounds are extensively metabolized by fish and higher organisms, so biomagnification in the food chain is limited. The amount of PAHs found in food also is affected by the method of preparation (grilling or smoking increases the amount of PAHs in food). The food chain would not appear to be an important source of human exposure to PAHs at this site based on the limited biomagnification of these compounds and the lack of continuous exposure.
B. Health Outcome Data Evaluation
Census data provide some background for evaluation of the health outcome data. Table 10 gives
the 1980 -1986 Census information for St. Mary Parish.
| Table 10 | ||||
| Census Data | ||||
| United States | Louisiana | St. Mary Parish | Morgan City | |
| 1980 Land Area (square miles) |
3,539,289 | 44,521 | 613 | |
| 1980 Population | 226,546,000 | 4,206,000 | 64,253 | |
| 1986 Population | 241,078,000 | 4,501,000 | 64,300 | 16,030 |
| 1986 Pop./sq. mile | 68.1 | 101.1 | 104.9 | |
| 1984 % White Pop. % Nonwhite Pop. |
85.1 14.9 |
68.8 31.2 |
66.8 33.2 |
|
1984 Age Group
5 - 14 years 15 - 24 years 25 - 44 years 45 - 64 years > 65 years |
7.6% 14.4% 17.0% 30.4% 19.0% 11.7% |
8.9% 16.2% 18.5% 29.8% 17.0% 9.3% |
9.7% 17.8% 19.4% 29.7% 15.8% 7.7% |
|
| 1984 Births *Rate |
3,669,141 15.5 |
81,472 18.3 |
1,356 20.9 |
|
| 1984 Total Deaths #Rate Infant Deaths |
2,039,369 8.6 39,580 |
35,741 8.0 982 |
476 7.3 12 |
|
| 1985 Per Capita Income | $10,797 | $8,836 | $8,768 | $10,360 |
| 1979 Percent Below Poverty Families |
12.4% 9.1% |
18.6% 15.7% |
15.6% 12.6% |
|
| * Per 1,000 resident population # Per 1,000 resident population @ Per 1,000 live births Reference: D-77 | ||||
Review of the census data suggests there is a younger population in Louisiana and St. Mary Parish than in the nation as a whole. St. Mary Parish has a high nonwhite population and larger numbers of people live below the poverty level than in the United States as a whole. Morgan City has a higher per capita income than either the parish or the state and approaches the per capita income of the United States. In 1985, Louisiana ranked 40 among the 50 states in per capita income. The influence of a large minority population and low economic status must be considered when examining health parameters for the area. Racial and ethnic groups have different health problems. For example, sickle cell anemia is much more common in individuals of African descent (R-85). Socioeconomic status can affect overall health of a community, thus influencing the community's susceptibility to certain diseases. Poor nutrition, crowding, and limited access to health care are some factors resulting from low economic status that affect health.
Numerous community concerns exist about adverse health effects from exposures that might
have occurred during 1986 and 1987. Tables 11a and 11b review the vital statistics St. Mary parish and Louisiana for those two years.
| Table 11a | |||
| 1986 Vital Statistics | |||
| Outcomes | Louisiana | St. Mary | Morgan City |
| Live Births: Total
White Nonwhite Rate: LB/1,000 Population |
77,944
45,648 32,296 17.3 |
1,221
726 495 18.8 |
309
207 102 18.1 |
| Immature Births: Total
White Nonwhite |
6,762
2,681 4,081 |
43
16 27 |
|
| Stillbirths
Rate:(Per 1,000 Live Birth) |
680
8.7 |
11
9.0 |
|
Rate/1,000 Population |
36,287 8.1 |
459 7.1 |
125 7.3 |
Malignant Neoplasms Cerebrovascular Diseases Accidents COPD & Related Disorders Suicide
Chronic Liver Disorders Congenital Anomalies (*):Rate/1000 Population |
12,728 (2.8) 8,036 (1.8) 2,578 (0.57) 2,014 (0.45) 1,017 (0.23) 648 (0.14) 507 (0.11) 622 (0.14) 380 (0.08) 269 (0.06) |
151 (2.3) 104 (1.6) 40 (0.62) 42 (0.65) 8 (0.12) 12 (0.18) 4 (0.06) 5 (0.08) 4 (0.06) 3 (0.05) |
|
| COPD -- Chronic Obstructive Pulmonary Disease (lung diseases)
Reference: D-75 | |||
| Table 11b | |||
| 1987 Vital Statistics | |||
| Outcomes | Louisiana | St. Mary | Morgan City |
| Live Births: Total
White Nonwhite Rate: LB/1,000 Population |
73,953
42,740 31,213 16.6 |
1,157
661 496 18.2 |
330
215 115 20.1 |
| Immature Births: Total
White Nonwhite |
6,408
2,546 3,862 |
20
7 13 | |
| Stillbirths
Rate:(Per 1,000 Live Birth) |
605 8.2 |
7 6.1 |
2 6.1 |
Rate/1,000 Population |
36,428 8.2 |
442 7.0 |
131 8.0 |
Malignant Neoplasms Cerebrovascular Diseases Accidents COPD & Related Disorders Suicide
Chronic Liver Disorders Congenital Anomalies (*):Rate/1000 Population |
13,050 (2.9) 8,119 (1.8) 2,517 (0.56) 1,842 (0.41) 1,073 (0.24) 559 (0.15) 454 (0.12) 570 (0.15) 347 (0.10) 269 (0.07) |
162 (2.6) 97 (1.5) 30 (0.47) 27 (0.43) 12 (0.19) 1 (0.02) 10 (0.16) 5 (0.08) 4 (0.06) 6 (0.09) |
|
| COPD -- Chronic Obstructive Pulmonary Disease (Lung Diseases)
Reference: D-76 | |||
| Table 12 | |||||||||||||||
| Congenital Malformations | |||||||||||||||
| Code | Malformation | Louisiana | St. Mary | ||||||||||||
| 81 | 82 | 83 | 84 | 85 | 86 | 87 | 81 | 82 | 83 | 84 | 85 | 86 | 87 | ||
| 740 | Anencephalus | 14 | 15 | 7 | 10 | 9 | 16 | 6 | 1 | 1 | 1 | ||||
| 741 | Spina Bifida | 22 | 19 | 20 | 28 | 25 | 20 | 21 | 2 | 1 | 1 | 1 | |||
| 742 | Other Nervous System | 12 | 26 | 14 | 17 | 23 | 21 | 22 | 1 | ||||||
| 744 | Ear, Face, and Neck | 12 | 19 | 25 | 20 | 20 | 47 | 29 | 1 | 5 | 1 | ||||
| 745 | Bulbus Cordis and Cardiac Septal Closure | 5 | 9 | 8 | 14 | 12 | 9 | 13 | 1 | 1 | 1 | ||||
| 746 | Other Heart | 15 | 22 | 13 | 31 | 26 | 26 | 22 | 1 | 1 | 2 | ||||
| 747 | Other Circulatory System | 15 | 15 | 10 | 14 | 19 | 10 | 7 | 1 | 1 | |||||
| 749 | Cleft Palate and Lip | 43 | 55 | 46 | 49 | 49 | 50 | 44 | 2 | 2 | 2 | 1 | 1 | 1 | |
| 750 | Other Upper Alimentary Tract | 11 | 10 | 14 | 10 | 7 | 15 | 14 | 1 | ||||||
| 751 | Other Digestive System | 13 | 20 | 12 | 17 | 11 | 11 | 10 | 1 | ||||||
| 752 | Genital Organs | 57 | 59 | 56 | 62 | 89 | 93 | 85 | 3 | 2 | 3 | 4 | 8 | 4 | |
| 753 | Urinary System | 5 | 13 | 13 | 18 | 14 | 16 | 22 | 1 | ||||||
| 754 | Certain Musculoskeletal Anomalies | 86 | 84 | 66 | 66 | 56 | 70 | 67 | 2 | 3 | 4 | 2 | 1 | 4 | |
| 755 | Other Limb Anomalies | 173 | 156 | 151 | 148 | 150 | 189 | 172 | 8 | 5 | 4 | 4 | 4 | 4 | 7 |
| 756 | Other Musculoskeletal | 37 | 34 | 29 | 28 | 44 | 92 | 44 | 1 | 1 | 2 | 1 | 8 | 3 | |
| 757 | The Integument (skin) | 30 | 35 | 30 | 50 | 40 | 111 | 73 | 1 | 1 | 4 | 10 | 3 | ||
| 758 | Chromosomal | 19 | 28 | 29 | 27 | 29 | 20 | 34 | 2 | 1 | 1 | 1 | |||
| 759 | Other and Unspecified | 15 | 22 | 38 | 36 | 48 | 31 | 26 | 1 | 1 | |||||
| 743 | Eye | 7 | 12 | 6 | 4 | 19 | 5 | 19 | |||||||
| 748 | Respiratory System | 8 | 17 | 17 | 18 | 7 | 12 | 13 | |||||||
| Total Malformations | 599 | 670 | 604 | 667 | 697 | 864 | 743 | 21 | 12 | 13 | 17 | 23 | 42 | 27 | |
| Reference: D-85 | |||||||||||||||
Congenital malformations were identified in approximately 1% of live births in Louisiana for the years 1984, 1986, and 1987. A larger number of children with malformations was identified in 1986. St. Mary Parish had 1% of live births identified as having malformations in 1984, 3% in 1986, and 2% in 1987. The typical incidence of congenital malformations identified on birth certificates is 0.5% to 1%. If hospital discharge diagnoses are used, the incidence is between 2% and 4% (R-54). Louisiana and St. Mary had a cause-specific mortality rate for congenital malformations of 0.06/1000 in 1986 (R-54). That rate is consistent with the natural average of cause-specific mortality. The number of malformations in St. Mary Parish was higher in 1986 than in previous years. Louisiana also noted a larger number of cases in 1986, but it was not at the proportion noted at the parish level. Several parishes in the northern half of the state also experienced a rise in the number of malformations in 1986 similar to that seen in the area around St. Mary.
Both Louisiana and St. Mary experienced an increase in anomalies of the skin, ear, face, and neck anomalies; and those classified as other musculoskeletal anomalies. A review of congenital malformations in St. Mary showed that 27 of the 42 were minor anomalies such as skin tags, cafe au lait spots, and undescended testicles. The number of malformations identified in both St. Mary Parish and Louisiana was lower in 1987 than in 1986. The reasons for the fluctuations are not known, but fluctuations are common in this type of data.
St. Mary has had a higher incidence of spina bifida than the national average in the past. That experience is unusual considering that there is a large African-American population in the area compared to the national average. Spina bifida occurs less frequently among blacks than among whites or other races (R-82). ATSDR does not have information on the racial make-up of the children with spina bifida. Louisiana has a greater black population and a lower rate of spina bifida than the United States. Several parishes in the Louisiana Health Service Area 2 were considered to have a high incidence of spina bifida, which did not change from 1983 to 1987. The incidence of spina bifida was high in 1983, before MSP began operation. Therefore, the rate of spina bifida in the parish appears to be unrelated to exposures from the facility.
Cancer incidence in southern Louisiana is lower than in the United States as a whole for the category of total cancer. The rate of lung cancer is higher than the U.S. rate for males. The Lafayette Region, which includes St. Mary Parish, has lower rates than the overall rates for southern Louisiana.
During 1986 and 1987, an excess of neuroblastoma cases was reported in St. Mary Parish (Expected: 0.4 cases, Observed: 4 cases). A case-control study by the Epidemiology Section of the Department of Pathology at Louisiana State University Medical School investigated the cluster. The cases included four children from St. Mary Parish and one child from Assumption Parish, whose mother had worked in St. Mary during her pregnancy. Cases were compared with two control groups: a sample of children born in the same hospital as the cases and a sample of children born in Bogalusa, LA. The study focused on exposures before and during pregnancy. Examination of environmental exposures such as drinking water source, residential proximity to industry, and pesticide treatments did not indicate that cases had increased exposure. No occupational or industrial exposures were significantly different between cases and controls. See Appendix A for a complete discussion of this study.
It is extremely difficult to identify causative agents in investigations of neighborhood clusters of disease, particularly if the cluster occurred during a specific period and is not ongoing. Identifying an environmental exposure that might have caused a chronic disease, such as cancer, is difficult because of the long latency period, and because exposures can occur by way of environmental routes such as air, water, or dust. Because everyone in the area is exposed to some extent to water, air, or dust, it is difficult to correlate an individual's exposure with a specific outcome (R-53).
Neuroblastoma is a primitive tumor of the sympathetic nervous system arising most commonly in the retroperitoneal area (the adrenal medulla is the most common site). The tumors metastasize early to the bones, lymph nodes, liver, and subcutaneous tissue. Neuroblastoma accounts for 8% of all childhood cancer in the United States; about 500 new cases are diagnosed annually. In infants, it is the most commonly diagnosed malignant. Fifty percent of neuroblastomas are diagnosed during the first two years of life; more than two thirds are diagnosed before age 5. Because the majority occur at such young ages, many researchers believe the tumor originates before birth. It is less common in black children than white children, suggesting that race could play a role in the etiology. Multiple cases of the disease in some families suggest there could be inherited susceptibility (R-45, R-42, R-55, R-60, R-37, R-59, R-13, R-41, R-26, R-83, R-20, R-74, R-25).
Many factors have been investigated for links to neuroblastoma, however, no factor has been consistently associated with an increase risk of neuroblastoma in those investigations. Birth weight above 4,000 grams has been suggested to be a factor in cancers before age 2 (R-24). A significant increase of breast cancer in mothers of children with solid tumors was seen at one referral unit (R-72). Cytomegalovirus infection has also been suggested as an etiologic agent (R-78). The occurrence of two cases of neuroblastoma in children with fetal hydantoin syndrome suggested a possible link to maternal Dilantin use in pregnancy (R-48). Fetal hydantoin syndrome is a group of birth defects seen in infants of mothers who used seizure prevention medications (such as Dilantin) during their pregnancies. A large case-control study in Minnesota did not identify any associations between neuroblastoma and complications of pregnancy, high birth weight, or shorter gestational period (R-52).
A study investigating medical and drug risk factors for neuroblastoma found associations with maternal use of alcohol, neurally active drugs, sex hormones, hair-coloring agents, antinausea medication, and diuretic use for water retention during pregnancy. Familial factors, parental cancer, irradiation, and cigarette smoking were not associated (R-41).
Recent epidemiological studies of parental occupation and neuroblastoma have suggested a link between parental employment in occupations with electromagnetic field exposure and neuroblastoma (R-70, R-15, R-81). That association was not significant in a study by Bunin et al. In summary, there has been no consistent link between neuroblastoma and any environmental causative agent.
The community has expressed concern about possible exposure to Dinoseb which was incinerated at the MSP facility in January and July, 1987. The concern is related to the fact that Dinoseb, a nitrophenol agent used as an insecticide and herbicide, was one of four pesticides targeted for further study in the report on a cluster of childhood cancers in McFarland, California. McFarland is a small town north of Bakersfield in which 13 cases of childhood cancer occurred between 1975 and 1989. Only four cases would have been expected during that time period based on typical incidence patterns. Only one of the cases in McFarland was a neuroblastoma. To date, no common exposure has been identified (R-19). Dinoseb has been shown to be a reproductive toxicant in animals, but not a carcinogen.
Because there was no definite environmental exposure identified for the children with neuroblastoma, it is not likely that any study could make a link to any single facility.
Numerous health parameters of concern have been identified in the community, such as the spina bifida rate elevated above the usual rates, the higher than expected rate of congenital malformations, and the previous cancer excess. Most of those parameters, however, have been elevated for many years, and it is not possible to link them specifically to exposures from MSP. The review of health outcome data for this public health assessment indicates that the contaminants identified at the facility have not been shown to cause the health problems that the community is concerned about. A more indepth study of the area might provide additional information that would indicate some link between those adverse health effects and an environmental exposure.
C. Community Health Concerns Evaluation
1. Safety of the aggregate
As noted in the Toxicological Evaluation section the available information does not suggest that anyone would be likely to ingest enough of the aggregate to risk intoxication from metals in the aggregate. However, there are very few data on the body burden resulting from long-term, low-level exposure to the aggregate. Specifically, there is insufficient information to determine the public health impact of the use of the aggregate on roadways and other areas where crushing and dust generation might occur or the use in areas where children may have chronic contact with the aggregate. ATSDR is concerned about any potential source of environmental lead exposure for children. Lead tends to stay in the body a long time once it is absorbed. To determine the safety of the aggregate requires additional information that considers the fact of increasing body burden of lead from chronic low-level exposures. That chronic problem is one of the major reasons the U.S. Public Health Service has developed a strategy to reduce exposures to lead from all potential environmental sources.
2. Contamination of Bayou Boeuf
As discussed in the Human Exposure Pathways section, exposure to site contaminants in the bayou is not likely to be of public health concern. However, ATSDR received limited data for evaluation of this concern.
3. Stack emissions
Based on the information discussed in the Environmental Contamination and Pathways Analyses sections, human exposure to stack emissions from the MSP site is unlikely to be of public health concern.
4. Clusters of neuroblastomas in the area
The incidence of neuroblastomas and other health concerns were discussed in the Health
Outcome Data Evaluation section. Using available information, it is not possible to link the
increased number of neuroblastomas in the area in 1986 with exposures to contaminants at the
MSP site. A community health investigation will be conducted to better assess this adverse
health outcome and other health concerns expressed by the community living near the site.
