PUBLIC HEALTH ASSESSMENT
ONONDAGA LAKE ENVIRONMENTAL CONTAMINATION AND OTHER HAZARDS
SYRACUSE, ONONDAGA COUNTY, NEW YORK
To evaluate if a site poses an existing or potential hazard to the exposed or potentially exposed population(s), the site conditions are characterized. This site characterization involves a review of sampling data for environmental media (e.g., soil, surface water, groundwater, air) both on- and off-site and an evaluation of the physical conditions of the contaminant sources or physical hazards near the site which may pose an additional health risk to the community or receptor population(s).
Contaminants selected for further evaluation are identified and discussed based upon consideration of the following factors:
The identification of a contaminant does not necessarily mean that it will cause adverse health effects from exposure. Contaminants selected for further evaluation are evaluated in subsequent sections of the PHA to determine whether exposure to them has public health significance.
The On-Site Contamination and the Off-site Contamination subsections include discussions of
sampling data for environmental media. If a chemical is selected for further evaluation in one
medium, that contaminant will also be reported in all other media, if it is detected.
A. On-site Contamination
Surface Water
Several metals have been identified in Onondaga Lake. Water samples from the uppermost layer of the water column and lowermost layer of the water column have been analyzed for organic compounds (i.e., benzene, toluene, ethylbenzene, xylene and chlorinated benzenes). The concentrations of the compounds detected are generally lower than the NYS DOH drinking water and the NYS DEC Class A surface water (drinking water source) standards, with the exception of chloride. High concentrations of chloride (about 500 milligrams per liter, or mg/L) which exceed the NYS DOH drinking water and the NYS DEC class A surface water standards (250 mg/L), have been detected in the lake water (PTI, 1993a). The drinking water standard for chloride is based on taste; however, since the lake is not used as a drinking water supply, the chloride contamination will not be considered further. Some of the samples taken by Onondaga County in 1987-1990 were reported to have cadmium and lead at levels equal to or slightly above the NYS DOH drinking water standards or action levels. However, more recent sampling ( PTI, 1993a) did not confirm these results. Although some samples contained levels of antimony (about 25 micrograms per liter, or mcg/L) and manganese (about 650 mcg/L only in deep water, i.e., 12 meters) which exceed the NYS DEC class A surface water standards or guidance values, none exceeded health assessment comparison values for recreational exposure to surface water (Table 1, Appendix B).
Fecal coliform and streptococcal bacteria in Onondaga Lake have been monitored since 1974. Levels of bacteria have declined since then, but are still present (PTI, 1991) at concentrations which occasionally exceed the NYS DOH standards for bathing beaches (refer to Table 2, Appendix B). The public health significance of bacterial contamination of the lake will be considered further in the PHA. Recently, dichlorobenzenes, naphthalene, xylenes and alkyl benzenes and two previously unidentified compounds (1-phenyl-1-(4-methylphenyl)-ethane and 1-phenyl-1-(2,4-dimethylphenyl)-ethane) were found in the water at the southern end of the lake; however, no concentrations were reported (Hassett, 1994).
Although the lake water is generally considered to be horizontally well mixed and homogenous, there is the potential for higher concentrations of contaminants near localized sources. Due to the lake stratification the concentrations of some compounds varied with water depth, and the sampling and analysis took this into account. A visible petroleum sheen was noted on the water surface in two areas at the southern end of the lake (PTI, 1993a).
Sediments
The lake sediments have been studied extensively, and contain many chemicals at concentrations above typical background concentrations. The type of contamination in lake sediments varies; generally, the southeastern part of the lake below Ninemile Creek is more heavily contaminated than the northwestern regions of the lake.
Mercury has been found in the sediment throughout the lake and at various depths. Mercury is unevenly distributed throughout lake sediment. The surface sediments in the lake near the shoreline tend to have lower contaminant concentrations than the sediments in the lake at distances further from the shoreline (PTI, 1991). The mean (average) detected concentration of mercury in the surface sediment is 3.8 milligrams per kilogram (mg/kg), about 7.7 times higher than the background concentration (PTI, 1993a). The range of concentrations of mercury in the surface sediment is 0.15 mg/kg to 68.9 mg/kg. Deeper samples had a higher mean of detected values (13.9 mg/kg), though the range was comparable.
Several additional metals were also found in lake sediments. The average concentration detected in the surface sediment for cadmium (2.5 mg/kg), chromium (79.3 mg/kg), copper (44.9 mg/kg), nickel (26.6 mg/kg) and zinc (110 mg/kg) exceeded typical background ranges for metals in soils. The average concentrations for deeper sediment samples were generally two to three times higher than the surface sediment concentrations. Barium, cadmium, and lead were detected in some of the sediment samples at concentrations above naturally occurring levels for NYS soils (NYS DEC, 1989). The concentrations of antimony and manganese in lake sediments were within the background range for NYS soils. No metals were detected at concentrations exceeding health assessment comparison values (see Table 3, Appendix B).
Several volatile organic compounds (VOCs) and semivolatile organic compounds (SVOCs) were detected in some sediment samples (PTI, 1993a), including benzene (up to 5.7 mg/kg), toluene (up to 4.2 mg/kg), chlorinated benzenes (e.g., monochlorobenzene up to 43 mg/kg; 1,4-dichlorobenzene up to 16 mg/kg; and hexachlorobenzene up to 1.2 mg/kg), bis(2-ethylhexyl)phthalate (up to 3 mg/kg), and PCBs (up to 1.1 mg/kg). The average concentrations of total polycyclic aromatic hydrocarbons (PAHs) detected exceed background levels; the higher concentrations were found in the southeastern portion of the lake. In addition, several different benzene compounds, PAHs, and aliphatic hydrocarbons were tentatively identified in some sediment samples (PTI, 1993a). Petroleum hydrocarbons were also detected at extremely elevated concentrations (up to 47,000 mg/kg) in sediment samples at the southern end of the lake (PTI, 1993a). The petroleum hydrocarbons detected have not been adequately characterized to evaluate possible public health implications. This represents a data gap that precludes further evaluation of petroleum hydrocarbons in this PHA. Although concentrations were not quantified, 1-phenyl-1-(4-methylphenyl)-ethane and 1-phenyl-1-(2,4-dimethylphenyl)-ethane were also detected in sediment at the southern end of the lake ( Hassett, 1994). A potential source of these compounds are the tar beds.
There are no comparison values for evaluating exposure to metals or organic compounds in lake sediments. However, soil comparison values do exist and the concentrations for metals above background do not exceed comparison values for soil in a non-residential setting (Table 3, Appendix B). Therefore, metals found in the lake sediment will not be considered further in this health assessment. With the exception of PAHs, the values of the organic compounds detected did not exceed health comparison values for soil in a non-residential setting and will not be evaluated further in this PHA.
For some of the PAHs detected in lake sediments there are no comparison values. For these compounds, the comparison value for benzo(a)pyrene was used to evaluate concentrations of carcinogenic PAHs and the comparison value for pyrene was used to evaluate concentrations of non-carcinogenic PAHs. The average concentration of all carcinogenic PAHs detected exceeds comparison values for soil in a non-residential setting. The public health significance of PAHs will be considered further in the Pathways Analysis section of this PHA.
Fish
Studies of fish in Onondaga Lake by the NYS DEC have found mercury concentrations which exceed the U.S. Food and Drug Administration (US FDA) action level (1 mg/kg) and health assessment comparison values (Table 4, Appendix B) in several fish species collected from the lake. In 1970, the first year that fish data were available from Onondaga Lake, the mean mercury concentrations in thirteen different species ranged from 0.4 to 5.3 mg/kg. The highest mercury level reported for an individual fish was 8.2 mg/kg. Based on these data, a fishing ban in Onondaga Lake was issued in 1970. Mean concentrations of mercury in fish from Onondaga Lake have varied since 1970; between 1970 and the mid-1980's, a general trend towards reduced mercury concentrations in fish was observed. In the mid-1980s, mean mercury concentrations in smallmouth bass was 1.2 mg/kg and in walleyes was 1.6 mg/kg. Individual fish from other species also had mercury concentrations that were greater than 1 mg/kg. Additional data for smallmouth bass, from 1987 to 1990, suggest that mercury levels in this fish species increased compared with earlier (mid-1980's) sampling data (average concentration about 1.6 mg/kg). Samples of smallmouth bass collected in 1992 had mean mercury concentrations of 0.91 and 0.75 mg/kg in two different studies; a peak concentration of 3.4 mg/kg was also reported (PTI, 1993b; NYS DEC, 1994). However, legal-size smallmouth bass (>12 inches) had a mean mercury concentration which exceeded the US FDA action level. In 1992, mean mercury concentrations for walleye were 1.5 and 2.3 mg/kg and about 1.1 mg/kg for white perch (PTI, 1993b; NYS DEC, 1994). Gizzard shad, carp, channel catfish, and bluegill had mean mercury concentrations below the US FDA action level. From 1970 to 1992, the mercury concentration in individual smallmouth bass has ranged from 0.4 mg/kg to 3.4 mg/kg.
PCBs have been detected in several different fish species from Onondaga Lake, occasionally at concentrations exceeding the US FDA tolerance level (i.e., 2 mg/kg), and health assessment comparison values (Table 4, Appendix B). Smallmouth bass collected in 1972 and 1979, had mean PCB concentrations of 0.71 and 1.1 mg/kg respectively; white perch collected in 1972 had mean PCB concentration of 1.6 mg/kg (NYS DEC, 1981). However, sampling of both of these fish species in 1975 showed mean PCB concentrations of 4.95 mg/kg for smallmouth bass and 4.72 mg/kg for white perch ( Armstrong and Sloan, 1980). In 1985, ten different fish species were sampled by the NYS DEC, and only channel catfish had a mean PCB concentration which exceeded the US FDA tolerance level (PTI, 1993b). In 1992, gizzard shad had a mean PCB concentration of 2.2 mg/kg, and nine other species of fish had average PCB concentrations between 0.1 mg/kg and 1.5 mg/kg (PTI, 1993b; NYS DEC, 1994). Some individual channel catfish and walleye contained PCBs at concentrations of 4.7 mg/kg and 3.1 mg/kg, respectively. Some smallmouth bass, channel catfish and white perch collected in 1992 as part of a limited study had PCB concentrations which exceeded 2 mg/kg (Stearns and Wheler, 1993).
Fish collected from Onondaga Lake in 1980 had detectable levels of monochlorobenzene, dichlorobenzene and benzene at concentrations ranging from 0.2 to 0.8 mg/kg (reviewed in PTI, 1991). 1,4-Dichlorobenzene, cadmium, lead, phthalates, hexachlorobenzene, chlorinated dibenzofurans, DDT and other contaminants were also detected in fish collected from Onondaga Lake in 1992 (PTI, 1993b; Stearns and Wheler, 1993). Although not quantified, 1-phenyl-1-(4-methylphenyl)-ethane and 1-phenyl-1-(2,4-dimethylphenyl)-ethane were also detected in fish (Hassett, 1994).
Mercury and PCBs will be evaluated further in this PHA. Due to the limited data about other contaminants, including cadmium, chlorinated dibenzofurans, benzene, monochlorobenzene and dichlorobenzene found in fish collected from Onondaga Lake, they will not be considered for further evaluation in this PHA.
Shoreline Soil
The shoreline soil has been investigated for potential chemical contaminants; however, the primary emphasis of these investigations has been on the industrial regions in the southeastern portion of the lake. Soda ash wastes (Solvay) have been deposited in several waste beds along the southwestern portion of the lake (Figure 3, Appendix A). These waste beds generally contain inorganic salts such as calcium chloride, sodium chloride, calcium carbonate, calcium silicate, magnesium hydroxide and calcium hydroxide (Blasland and Bouck Engineers, 1990). The waste beds are alkaline and surface water drainages from the waste beds have pHs that range from 7.5 to 10.6. In addition, wastes containing tar, benzene, toluene, xylene and PAHs from a plant that refined coke light oil were deposited about 200 feet from the shoreline in the Semet residue ponds (tar beds) that were built on top of a soda ash wastebed. Benzene, toluene, chlorobenzene and dichlorobenzene have been detected in the soil between the tar beds and Onondaga Lake (Groundwater Technology, Inc., 1993). Odors from the tar beds have been detected by the NYS DOH personnel several miles from the site, including in several parts of the City of Syracuse. There is a large bulk petroleum storage/terminal facility, known as Oil City, on the shoreline. The presence of petroleum products in lake sediment suggests that there may be petroleum products contaminating the shoreline soil.
Data are not available for other portions of the shoreline. However, a 1973 report describes some sediment dredging operations in the outlet barge canal, the oil terminal area, and the delta near the mouth of Ninemile Creek (US EPA, 1973). The disposition of most of the dredged sediments was not reported and is not currently known. The delta near the mouth of Ninemile Creek was dredged in 1968 and the dredge spoils were disposed in a low area just north of the creek which was being developed as a recreational park. These spoils have not been analyzed for potential contaminants.
Waterfowl
Potential contaminants in waterfowl present in the Onondaga Lake region have not been characterized. However, it is known that PCBs and mercury, which have been detected in fish in Onondaga Lake, can bioaccumulate in waterfowl.
Air
There are no data from the lake pertaining to surface water releases of compounds. However,
volatilization of contaminants from lake surface water, especially mercury, is a possibility.
Odors from the tar beds vary and tend to be stronger in the warmer weather and have been
detected by local health officials two to three miles away. Therefore, depending on the wind
direction, air quality at or near the lake can be affected by odors from the tar beds. Elevated
levels of benzene have been detected by the NYS DEC, the NYS DOH and the Onondaga
County Health Department in the region near the tar beds.
B. Off-site Contamination
Surface Water
Surface water exiting the lake at the northwest corner has not been characterized for potential contaminants but it is assumed to be similar to the surface water quality in the lake. The water from Ley Creek has been analyzed and detectable concentrations of PCBs have been reported (O'Brien and Gere Engineers, Inc., 1993). The water from Ninemile Creek has been sampled and several contaminants including mercury were identified ( CDR Environmental Specialists, 1991). The Metro plant has also been identified as a significant source of mercury entering the lake (Driscoll and Wang, 1994). Approximately 48% of the mercury currently entering the lake has been attributed to Ninemile Creek, and 25% has been attributed to the Metro plant (Driscoll and Wang, 1994).
Sediment
Sediments in the Barge Canal in the northwest corner of the lake and further downstream (i.e., Seneca River) have not been characterized for potential contaminants. As with the surface water of the tributaries to the lake, there has been some characterization of the sediments in some of the tributaries. Mercury has been detected in the sediments of Ninemile Creek at concentrations that are higher than background levels for NYS soils, and PCBs have been detected in Ley Creek (CDR Environmental Services, Inc., 1993; O'Brien and Gere Engineers, Inc., 1993).
Fish
Contaminant levels in fish from the Barge Canal at the northwest corner of the lake and further downstream (i.e., Seneca River) have not been characterized. Studies of fish movement for fish initially caught in Onondaga Lake have indicated that some fish leave the lake via the outlet and have been found as far up the Seneca River as Baldwinsville (about six miles), and as far down river as Fulton (about 16 miles).
In 1990, limited sampling of fish from Ninemile Creek and Geddes Brook found smallmouth bass with approximately 1.5 mg/kg mercury and other species of fish contained mercury at levels which ranged from 0.055 to 0.635 mg/kg (CDR Environmental Specialists, 1991). Some of the fish caught in Ley Creek have been reported to have greater than 2 mg/kg of PCBs (O'Brien and Gere Engineers, Inc., 1993). In addition, dioxins and dibenzofurans have been detected in fish caught in Ley Creek ( Estabrook, 1992).
Air
As mentioned previously, odors from the tar beds can be detected at distances two to three miles away. However, there is insufficient air sampling data and information to characterize possible exposures. AlliedSignal, Inc. is conducting a RI/FS on the tar beds. AlliedSignal, Inc. signed an Administrative Order on Consent (Dec. 15, 1994) agreeing to a temporary cover over tar bed ponds nos. 3 and 4, as an interim measure.
Groundwater
Onondaga Lake is a local groundwater discharge point and contaminants from the lake would not be expected to migrate to groundwater under non-pumping conditions (NYS DEC, 1989). During periods of flooding, local hydraulic gradients may be reversed and some water from the lake may discharge to groundwater as a short-term, temporary effect. The nearest homes to the lake served by groundwater wells are on Walters Road, about 1.5 miles from the lake boundary (NYS DEC, 1989). There are no other known private wells near the lake. Groundwater near the southwestern portion of the lake was analyzed for potential contaminants that may be transported to the lake. Several volatile organic compounds (e.g., benzene, toluene, xylene, chlorobenzene and dichlorobenzene) have been detected in the groundwater (PTI, 1993a). An interim remedial measure consisting of product recovery for a mixture of chlorobenzene and dichlorobenzene solvents has been initiated by Groundwater Technology, Inc. on behalf of AlliedSignal, Inc. (Groundwater Technology, Inc., 1993). Petroleum storage facilities near the southern end of the lake may contribute to groundwater contamination by petroleum products which could also be affecting the lake (Onondaga Lake Management Conference, 1993).
Soil
There are no data to characterize soils beyond the shoreline. As mentioned previously, lake
sediments were dredged and it is unclear where the spoils were disposed.
C. Quality Assurance and Quality Control
In preparing this public health assessment, the NYS DOH relies on the information provided in the referenced documents and assumes that adequate quality control measures were followed with regard to chain-of-custody, laboratory procedures and data reporting. The validity of the analyses and the conclusions drawn for this assessment are determined by the availability and reliability of the referenced material.
Some of the referenced reports did not have quality assurance/quality control (QA/QC) statements in their reports. However, it is assumed for the purposes of this public health assessment that the data reviewed are of acceptable quality.
Several of the reports (e.g.,PTI, 1993a,b; Blasland and Bouck Engineers, 1990) have not been
evaluated or approved by the NYS DEC for accuracy, QA/QC, or completeness. The reader
should be aware that references to these data are references to preliminary information only and
that inferences and conclusions based upon this draft data may be significantly revised following
the NYS DEC review of the data.
D. Physical and Other Hazards
Physical and other hazards are associated with the lake and shoreline. The lake water has high
turbidity, causing poor water clarity. Drowning is one hazard associated with recreational use of
the lake. Parts of the southern shoreline, near Ninemile Creek, are steep and rocky and access to
the lake along these areas is difficult and potentially hazardous. The soft and unstable inshore
bottom substrate (e.g., oncolites) created by past industrial waste discharges also presents a
physical hazard, particularly if swimming becomes a future lake use. The industrial and
commercial sites including the tar beds and some waste beds along the shoreline have not been
evaluated for physical and other hazards as part of this PHA.
E. Toxic Chemical Release Inventory (TRI)
To identify other facilities that could possibly contribute to site-related contaminants in soil, air, groundwater, and/or surface water at or near the Onondaga Lake site, or create health threats unrelated to the site, the NYS DOH searched the Toxic Chemical Release Inventory (TRI). The TRI has been developed by the US EPA from chemical release information provided by those industries that are required to report contaminant emissions and releases on an annual basis. The NYS DOH reviewed TRI data submitted by industrial facilities identified to be within a 2.5 mile radius of the perimeter of Onondaga Lake for the years 1988 through 1992 as a means to evaluate other sources of additional health risk in the exposed population.
The NYS DOH uses a simple mathematical model to estimate if potential contaminant concentrations resulting from air emissions at a facility may be contributing to community (receptor population) exposures to contaminants at a site. This model uses information about the facility location (distance from the exposed population) and annual air emission data to calculate the radial distance from the facility at which contaminant concentrations in ambient air are below screening criteria. For most contaminants the NYS DOH then evaluates what portion, if any, of the population living within this distance from the manufacturing facility may also be exposed to contaminants originating at the site.
Presently, there are 28 industrial facilities within about a 2.5 mile radius of Onondaga Lake (refer
to Figures 4 and 5, Appendix A). Additionally, H.P. Hood, Inc. and the Cambridge Filter
Corporation were also considered in this evaluation, since the facilities are situated near the 2.5
mile radius from Onondaga Lake. Those facilities which filed TRI data for 1992 include the
Syracuse Heating Corporation; Crucible, Inc. (Specialty Division); Chemtech Industries, Inc.;
Pass & Seymour; General Chemical Corporation; Church and Dwight Company, Inc.; Marcellus
Casket Company; Caldwell & Ward Brass Company; Boorum & Pease, Inc.; Anoplate
Corporation; Benbow Chemical Packaging, Inc; Syracuse China Corporation; Crouse-Hinds
Company (Wolf Street Plant); Meloon Foundries, Inc.; B.G. Sulzle, Inc.; Martin Marietta
-General Electric Company; Strathmore Products, Inc. (Plant #2); Syrtek, Inc. (formerly Pico
Products, Inc.); Deluxe Check Printers; and H.P. Hood. Summaries of the TRI-reported releases
to air, surface water and publicly owned treatment works by these facilities for the year 1992 are
presented in Tables 5 and 6 (Appendix B), respectively. Eight facilities did not file TRI data for
1992. These include LCP Chemicals; Frazer & Jones Company; Lipe-Rollaway Company;
Fastek; Strathmore Products, Inc. (Syracuse); R.E. Deitz Company; the GE Company (Farrel
Road Plant); and the Cambridge Filter Corporation. For those facilities that filed TRI data in
1992, the 1992 data appeared to adequately represent releases from previous years (i.e.,
1988-1991). For those facilities which did not file TRI data in 1992, data from previous years
were evaluated.
Church and Dwight Inc. is a potentially significant source of ammonia in the lake. In 1988,
LCP-Chemicals discharged mercury into surface water (110 lbs.) and publicly owned treatment
works (9 lbs.). In 1989 and 1990 no mercury releases were reported from LCP-Chemicals. In
addition, Crucible Inc. discharged manganese, nickel, chromium and copper into surface water
that enters the lake. The levels of mercury, manganese, nickel, chromium and copper in the
sediments exceed typical background concentrations for soils. The discharges from
LCP-Chemical and Crucible Inc. may have contributed to the concentrations found in lake
sediment. None of the other compounds released to surface water from TRI facilities between
1988 and 1992 had concentrations in lake sediment or lake water which exceeded comparison
values.
Results of the screening evaluation indicate that TRI-reported air emissions from the facilities
identified would not increase contaminant levels in ambient air near the Onondaga Lake site to
levels above the screening criteria of 0.1 micrograms per cubic meter (mcg/m3) for chromium,
0.02 mcg/m3 for nickel, 0.4 mcg/m3 for manganese, or 1 mcg/m3 for other compounds. Based on
the results of the screening evaluation, the public health significance of contaminant air
emissions and water discharges from TRI facilities as additional sources of community exposures
at the Onondaga Lake site will not be evaluated further in this public health assessment.
PATHWAYS ANALYSES
This section of the public health assessment (PHA) identifies potential and completed exposurepathways associated with past, present and future use of the site. An exposure pathway is the process by which an individual may be exposed to contaminants originating from a site. An exposure pathway is comprised of five elements, including: (1) a contaminant source; (2) environmental media and transport mechanisms; (3) a point of exposure; (4) a route of exposure; and (5) a receptor population.
The source of contamination is the source of contaminant release to the environment (any waste disposal area or point of discharge); if the original source is unknown, it is the environmental media (soil, air, biota, water) which are contaminated at the point of exposure. Environmental media and transport mechanisms "carry" contaminants from the source to points where human exposure may occur. The exposure point is a location where actual or potential human contact with a contaminated medium may occur. The route of exposure is the manner in which a contaminant actually enters or contacts the body (i.e., ingestion, inhalation, dermal absorption). The receptor population is the person or people who are exposed or may be exposed to contaminants at a point of exposure.
Two types of exposure pathways are evaluated in the PHA; a completed exposure pathway exists
when the criteria for all five elements of an exposure pathway are documented; a potential
exposure pathway exists when the criteria for any one of the five elements comprising an
exposure pathway is not met. A suspected exposure pathway is considered to be eliminated
when any one of the five elements comprising an exposure pathway has not existed in the past,
does not exist in the present and will never exist in the future. Because the primary routes of
exposure to site-related contaminants are due to recreational activities at the lake, it is difficult to
estimate the number of persons actually exposed. However, ATSDR and NYS DOH estimate
that 216,682 persons are potentially exposed to site-related contaminants. This estimate, based
on the 1990 census, is the total populations of the Towns of Salina and Geddes and the City of
Syracuse bordering Onondaga Lake.
A. Completed Exposure Pathways
Fish - Onondaga Lake Pathway
Data from as early as 1970 have shown that many species of fish from Onondaga Lake contain mercury and other contaminants. Prior to closing the lake to public fishing in 1970, people did fish in the lake and it is assumed that some fish were eaten. Prior to 1970, fish in Onondaga Lake most likely contained mercury and possibly other contaminants. In 1986, the fishing ban was dropped and the NYS DOH issued and has maintained a public health advisory not to eat fish from Onondaga Lake (refer to Appendix C). These actions are believed to have significantly reduced the amount of fish from Onondaga Lake which are eaten, although it is likely that some fish are still eaten.
Surface Water Pathway
Although swimming in the lake has been discouraged for quite some time and there are no
permitted bathing beaches, the lake is used for recreational and commercial boating. Exposure to
contaminants in lake water can occur via water skiing, wind-surfing, spray, handling fish,
splashes from oars and paddles, capsizes, wading, etc. Reportedly, swimming has occurred in
the lake. Prior to 1920, swimming routinely occurred in the lake, and people were most likely
exposed to chemical and bacteriological contamination. However, water quality and sediment
contamination at that time were not characterized and the public health implications of past
exposures from swimming in the lake prior to 1920 can not be evaluated.
B. Potential Exposure Pathways
Shoreline Pathway
A great deal of the shoreline, including soil, along Onondaga Lake is accessible to the public who could be exposed to contaminants by dermal contact, inhalation and ingestion. Soils along the shoreline have not been analyzed for chemical contaminants, and this is a data gap which prevents evaluation of possible past, present and future human exposure pathways to contaminants in soil. Reports of dredging spoils being used as fill just north of Ninemile Creek suggests that parts of the shoreline may be contaminated. Some of the waste beds in the southern portion of the lake are basic (i.e., alkaline) and are accessible to the public. The tar beds are in an industrial area and are fenced and posted. Therefore, they are not readily accessible to the public.
Sediments Pathway
Onondaga Lake sediments that contain elevated levels of PAHs were mostly localized in areas at the southeastern portion of the lake. This portion of the lake shoreline has not been developed for public beaches, swimming, or wading. Thus, potential exposure to PAHs in sediment is considered to be minimal at present. Persons could be exposed to PAHs in sediments if the sediments are dredged and placed in an area where they may be available for human contact, or if swimming in the lake occurs in the future. Therefore, a future potential human exposure pathway exists to PAHs in sediments of Onondaga Lake.
Fish Beyond the Northwest Outlet of the Lake and in the Tributaries
Water leaves the lake at the Northwest corner (Figure 1, Appendix A), and reportedly fishing occurs in this area. Fish in this region have not been well characterized for potential chemical contaminants and there is some evidence that fish originally caught in Onondaga Lake have migrated to the outlet and beyond. This is a data gap that prevents evaluation of possible past, present, and future exposure pathways through ingestion of fish beyond the lake boundary. Limited sampling of fish from tributaries to Onondaga Lake is inadequate to characterize possible past, present and future exposures through ingestion of fish from the tributaries.
Air
Ambient air quality at and near the lake and shoreline has not been well characterized. The tar beds tend to affect the air quality in the region and depending on the prevailing winds may impact air near the lake. In addition, odors from the tar beds can be detected two to three miles away, including within the City of Syracuse. Since the air quality near the lake has not been characterized, this is a data gap that prevents the evaluation of possible past, present, and future exposure pathways to contaminants from the tar beds through inhalation.
Waterfowl Pathway
Hunting of waterfowl at and near Onondaga Lake has been reported to occur and it is assumed
that waterfowl are eaten. Some of the waterfowl in the region are migratory. The accumulation
of contaminants from the lake in waterfowl is unknown, and this presents a data gap that
prevents the evaluation of possible past, present, and future human exposure to lake
contaminants through ingestion of waterfowl.
C. Eliminated Exposure Pathways
Groundwater
The lake is a local groundwater discharge point and groundwater flows into the lake.
Groundwater flow conditions could be temporarily reversed during flood conditions. However,
the effects of flooding are not expected to result in significant flow reversals. Commercial,
industrial and other properties closer to the lake are served by public water. The nearest homes
using groundwater for drinking are more than one mile away. The potential for exposure to
contaminants in groundwater is not expected to occur and this human exposure pathway is
considered to be eliminated and will not be evaluated further in this PHA.
PUBLIC HEALTH IMPLICATIONS A. Toxicological Evaluation
An analysis of the toxicological implications of the completed and potential human exposure pathways of concern is presented below. To evaluate the potential health risks from contaminants of concern associated with the Onondaga Lake site, the NYS DOH assessed the potential risks for cancer and noncancer health effects. The potential health risks are related to contaminant concentration, exposure pathway, exposure frequency and duration. For additional information on how the NYS DOH determined and qualified potential health risks applicable to this site, see Appendix D.
Since the 1970's, fish in Onondaga Lake have been found to be contaminated with mercury and PCBs. Chlorinated benzenes and cadmium have also been observed at moderate concentrations on various occasions. Prior to 1970, there was no ban on fishing, and fish were presumably caught and eaten. Between 1970 and 1986, fishing was banned, and this most likely had a significant effect in reducing consumption of contaminated fish. Since 1986, fishing has been permitted. However, the NYS DOH has maintained an advisory to eat no fish caught in the lake and its tributaries, to the first barrier impassable to fish (Appendix C). The amount of fish that might still be consumed is not known; however, the NYS DEC reports that fishing pressure is light. Fish in Onondaga Lake have been contaminated for an undetermined period of time and with a variable degree of contamination. Exposure will vary depending on species, number, size, and method of preparing and cooking the fish.
In the environment, natural biological processes convert mercury into methylmercury. Most mercury accumulated in fish tissues is methylmercury. This form is one of the most toxic forms of mercury and is readily absorbed by the intestine in man. In the human body, mercury accumulates in the liver, kidney, brain, and blood and can cause both acute and chronic health effects (ATSDR, 1992). Symptoms of chronic mercury poisoning include loss of appetite, weight loss, birth defects, and central nervous system and kidney damage. Consumption of fish containing relatively high levels of methylmercury has been associated with the widespread poisoning of fishermen and their families in Minamata, Japan. Other poisonings associated with the consumption of methylmercury-contaminated fish and grain have provided substantial data regarding the level of methylmercury consumption associated with adverse health effects. Pregnant women who eat a meal containing one-half pound of fish caught in Onondaga Lake containing approximately 1 mg/kg mercury exceeds the ATSDR's acute minimal risk level for developmental effects on the unborn child. The risk of adverse health effects to an unborn child by a pregnant woman eating mercury-contaminated fish from Onondaga Lake is high. These health effects could include brain damage, behavioral and developmental effects. The risk of adverse health effects to other people who eat one half-pound meal per week of fish from Onondaga Lake is low.
PCBs cause cancer in laboratory animals exposed to high levels over their lifetimes (ATSDR, 1991a). Whether PCBs cause cancer in humans is unknown. However, chemicals that cause cancer in laboratory animals may also increase the risk of cancer in humans exposed to lower levels over long periods of time. Based on the results of animal studies, the estimated increased risk of developing cancer from consuming one-half pound per week of fish from Onondaga Lake containing PCB contamination at 0.8 to 1.5 mg/kg is high. However, the existing information suggests that very few people, if any, are eating the fish.
Human health effects reported after occupational exposure to PCBs include skin, eye, and respiratory tract irritation and, less frequently, effects on the liver and the nervous and digestive systems (ATSDR, 1991a). Maternal exposure to PCBs may produce developmental effects on the unborn child. A New York State Health Department study of women exposed to PCBs in their workplace found evidence of a link between PCB exposure and lower birthweight children. There may be a link between a mother's increased exposure to PCBs and slight effects on her child's birthweight and behavior (ATSDR, 1991a; Rogan and Gladen, 1991, 1992). Recent evidence suggests that some behavioral anomalies and low birthweights occurred in infants whose mothers had a relatively high exposure to PCBs and other contaminants from the consumption of Great Lakes sportfish for many years before pregnancy. Neurological effects were also noted in some of the same children when they were 5 years old. In a second study conducted in North Carolina, behavioral anomalies, but not low birthweights, were found in newborns of women who had elevated blood PCB levels. Some of these same children showed neurological effects at 6, 12 and 24 months, but not at 3, 4 or 5 years of age. In both studies, the possibility that the women may have been exposed to other toxic chemicals was not completely examined. The effects of PCBs in animals include low birthweight, skin disorders, liver problems and damage to the immune and nervous systems. Chemicals that cause adverse health effects in humans and/or animals following high level exposure may also increase the risk of adverse health effects in humans exposed to lower levels over long periods of time. Although the risks of non-carcinogenic adverse effects from ingestion of PCB-contaminated fish are not completely understood, the existing data suggests that the increased risk of non-carcinogenic adverse health effects from eating one-half pound of fish per week containing approximately 0.8 to 1.5 mg/kg of PCBs exceeds the ATSDR's chronic minimal risk level. The risk of adverse health effects from eating one-half pound per week of PCB contaminated fish is high.
Exposure to lake water has been fairly restricted and only limited exposure during recreational activities is presumed to occur. The lake water is contaminated with fecal bacteria at levels which intermittently exceed the NYS DOH public bathing beach standards. Fecal coliform bacteria is an indicator of potential contamination by other bacteria and other organisms that can produce diseases such as gastrointestinal illness, hepatitis A, giardiasis, and shigellosis (i.e., dysentery). Recreational use of the lake, particularly swimming and wading activities poses a risk of serious adverse health effects when fecal coliform bacteria are elevated.
The lake sediments are contaminated with PAHs. PAHs can produce immunosuppression, bone marrow depression, reproductive/developmental effects and skin disorders in animals. The risks of non-carcinogenic adverse effects from PAH contamination of sediment is estimated to be minimal when associated with recreational use of the lake. Some PAHs have been reported to produce gastric, lung and skin tumors in animals (ATSDR, 1993). Whether PAHs which cause cancer in animals cause cancer in humans is not known. However, chemicals that cause cancer in laboratory animals may also increase the risk of cancer in humans exposed to lower levels over longer periods of time. Due to the limited access to lake sediments, the estimated increased risk of developing cancer from exposure to lake sediments during recreational activities is very low.
If the contaminated sediment is used as fill in residential or non-residential settings, the increased risk of cancer could be high; the increased risk of non-cancer effects could be moderate.
B. Health Outcome Data Evaluation
The NYS DOH evaluated cancer incidence in Clay, New York and concluded that for all cancer sites (combined) there was not a significantly different number of cancer cases for males or females than would be expected in other upstate New York communities (NYS DOH, 1985). Only the number of kidney cancers showed a statistically significant excess in males. Of the four kidney cancers observed, there were three different types. It was concluded by the investigators that the different cell types have different epidemiologic characteristics and that it was unlikely that they were associated with a common environmental cause.
The NYS DOH also evaluated the incidence of cancer in the Towns of VanBuren and Camillus (NYS DOH, 1990) in response to community health concerns about possible health affects related to a nearby dumpsite. For all cancer sites combined, the total incidence of cancer for both sexes in the study area was not significantly different from expected rates based on comparable communities.
The NYS DOH also has two other cancer incidence studies in progress in this area. For the first study, the study area is the Town of Geddes, which corresponds to census tract 128. This area borders on Onondaga Lake to the southwest. The study is expected to be completed in early 1996.
The second study in progress includes the Village of North Syracuse and parts of the Town of
Clay and the Town of Cicero (census tracts 105, 106, 107, 108, 109, 110.01 and 110.02). The
closest that this area comes to Onondaga Lake is about 1 1/2 miles from the lake. The study is
expected to be completed in late 1996 or early 1997.
C. Community Health Concerns Evaluation
This PHA has been prepared, in part, to address community health concerns about past exposures to contaminants at and near Onondaga Lake and the risk of developing cancer. Past studies of cancer occurrence in communities near Onondaga Lake by the NYS DOH have not shown statistically significant findings that might be related to a common environmental cause.
Community health concerns about 1) recreational use of the lake, 2) fishing and use of the shoreline, 3) odors emanating from the tar beds, and 4) possible impacts of the Oil City contamination and rehabilitation effort related to the lake and shoreline have been discussed previously in this PHA.
Recreational use of the lake represents a potential health hazard largely because of the fecal bacteria contamination. Ingestion of fish caught in Onondaga Lake represents a health hazard due to mercury and PCBs in the fish. The NYS DOH has issued an advisory recommending that people eat no fish caught in Onondaga Lake or its tributaries to the first barrier impassable to fish. Appendix C of this PHA contains a copy of the complete health advisory for 1994/1995. Contamination of shoreline soils in the area known as Oil City and elsewhere along the Lake has not been adequately characterized to evaluate potential health hazards. This PHA includes a recommendation that additional investigations be conducted to determine the degree and extent of contamination of the lake shoreline. The NYS DOH will review additional data that is developed for the Onondaga Lake site to evaluate the possible public health significance associated with use of the shoreline. The chemicals responsible for the tar bed odor have not been identified and an evaluation of possible related health implications has not been completed as part of this PHA. However, this PHA includes a recommendation that the chemicals contributing to the odors from the tar bed be identified. The NYS DOH will review data that is developed to evaluate the possible public health significance associated with odors from the tar beds. Additionally, the NYS DOH and the NYS DEC are negotiating with Allied Chemical for a temporary cover over the tar bed to reduce the odors.
Next Section
Table of Contents
