Preliminary Investigation Of The Extent And Effects Of Sediment Contamination In White Lake, MI

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4.5 Mercury Bioaccumulation

The bioaccumulation of mercury was investigated under laboratory conditions with Lumbriculus variegatus and in-situ with mesocosms. The laboratory bioaccumulation evaluation with Lumbriculus variegatus also included a four day toxicity screening test.

4.5.1 Lumbriculus variegatus Bioaccumulation Test

4.5.1.1 Preliminary Toxicity Screening Test

The preliminary toxicity screening of the White Lake sediments was initiated on October 19, 1996 and completed on October 23, 1996. Composite sediment samples collected on the same day from three different sites were employed in exposing L. variegatus over this period. Temperature and dissolved oxygen measurements were taken and recorded twice daily throughout the duration of the test (Appendix C: Table C-1). Temperature varied little, which was expected since the test beakers were kept in a temperature controlled room. The dissolved oxygen never dropped below 40% saturation; consequently, no aeration was required. Conductivity, hardness, alkalinity, ammonia, and pH were determined at the beginning and on the fourth day of the test, and these data are shown in Appendix C: Table C-2. With the exception of ammonia and alkalinity in sample I-7M, these parameters remained relatively constant, with a variation of less than 50%, from initial to final measurements.

The results of the four day toxicity test are provided in Table 4.5.1. The results suggest that these sediments were not acutely toxic to L. variegatus over the four day exposure period. Furthermore, any contaminants in the sediment did not seem to inhibit the oligochaetes from burrowing into the sediment. In light of these findings, it may be stated that the variation in the ammonia content and alkalinity in sample I-7M were not important factors in this preliminary screening.

Table 4.5.1
Summary Of Oligachaete Survival Data Obtained When Exposed To White Lake Sediments For Four Days

4.5.1.2 Bioaccumulation Test

The bioaccumulation test of the White Lake sediments was initiated on October 25, 1996 and completed on November 21, 1996. The same sediment samples used in the toxicity screening were used to expose L. variegatus for the 28 day test period.

As in the toxicity screening, temperature and dissolved oxygen measurements were taken and recorded twice daily throughout the duration of the test (Appendix C: Table C-3). Again, temperature varied little. However, in this test it was noted that the dissolved oxygen was not being maintained at the recommended 40% saturation level, as a result, aeration of the exposure chambers was initiated on day 5 of the test. Conductivity, hardness, alkalinity, ammonia, and pH were determined at the beginning and on the 7th, 14th, and final day of the test. These data are shown in Appendix C: Table C-4. Conductivity and pH remained relatively constant from initial to final measurements. Ammonia decreased by more than 80% in all three sediments, alkalinity dropped more than 60% in I-5M and I-7M, and hardness fell more than 50% in only the sediment from I-5M.

The results of the mercury analyses are summarized in Table 4.5.3. The mercury levels in the test organisms exposed to Tannery Bay sediments exhibited similar body burdens as the organisms exposed to the control sediment (E-1P). No significant mercury bioaccumulation was observed under laboratory conditions.

4.5.1.3 Reference Toxicity Test Results

The results of the reference toxicity test for L. variegatus are summarized in Appendix E.

Table 4.5.2
Results Of Mercury Bioaccumulation Experiments With
Lumbriculus variegatus

4.5.2 Mesocosms

The mesocosms were deployed near I-7M and E-1P. These points were located closer to the shoreline in both areas due to the depth limitation of the enclosures (3 m). Good recovery was obtained with the catfish from all replicates. Recovery of the fathead minnows however was poor. Low recoveries of the minnows may be a function of predation by the catfish, the recovery technique itself, or losses during the experiment. One of the mesocosms at the I-7M location changed dramatically after the first 10 days of exposure. The water turned black and exhibited a strong sulfur odor. All of the minnows and catfish died during this event. An analysis of the water found an ammonia concentration of 3.8 mg/l, which may have directly caused the toxic response. The loss of this mesocosm appears to be the result of a localized disturbance of the sediments. Gas production from the sediments (methane) may have caused the resuspension of fine particulates and the subsequent release of ammonia. Ammonia release from the sediments was observed during the toxicity experiments (Section 4.3).

The results of mercury analyses on the catfish are presented in Table 4.5.3. Initial mercury levels were similar to the concentrations observed the mesocosms located at Station E-1 and the Tannery Bay location. No evidence of mercury bioaccumulation was noted. These results were similar to the laboratory tests with Lumbriculus variegatus. Although elevated mercury concentrations are present in the Tannery Bay sediments, bioaccumulation does not appear to be significant during 30 day laboratory or in-situ mesocosm exposures.

Table 4.5.3
Results Of Mercury Analyses Conducted On Ictalurus punctatus
From The Mesocosms

4.6 Organic Analysis Of Selected Sediment Cores

The results of semivolatiles analyses conducted on the core samples for exterior stations E-7 and E-9 are displayed in Figure 4.6.1. As discussed earlier, Station E-9 was selected to determine if organic chemicals related to the historic discharge from the Hooker Chemical and Plastics facility were still present in White Lake. This facility began operations in 1954 and closed in 1982. The sampling station is located in the deep region near the historical effluent discharge. With the exception of trace amounts of 1,4-dichlorobenzene, none of the target analytes were present in the 0-15 inch region of the core. Detectable levels of dichlorobenzenes (2.4 mg/kg), hexachlorobenzene (2.1 mg/kg), and hexachlorobutadiene (0.66 mg/kg) were found in the 15-30 inch section. In addition, the GC/MS scan also identified PCBs and residues of mirex. The PCBs were confirmed by GC-ECD analysis, and the results are reported in Figure 4.6.1. Lower levels of the same chemicals were found in the 30-45 inch core section. The sections representing the 45-60 inch and the 60-90 inch regions contained no detectable target compounds. Using historical information concerning the Hooker Chemical discharge, the core region below 45 inches probably predates the mid 1950s. The region of 15-45 inches reflects the discharge of process effluent and contaminated groundwater into White Lake from 1954 to 1982. Because none of the chlorinated organic compounds were detected in the top 15 inches, these sediments probably represent material that was deposited after the mid 1980s.

The presence of high levels of PCBs in the 15-30 inch region is interesting in that this material has not previously been associated with the Hooker Chemical discharge. While the PCBs appear to be covered by 15 inches of stable sediment, the extent and source of contamination need to be investigated. Since the E-9 location appears to be a long term deposition zone for sediments from eastern White Lake, it is possible that the PCBs may have originated from a different location.

The deposition of the chlorinated organics at this location also provides information that is useful in the interpretation of the chromium data. The high chromium concentrations found in the top 15 inches of sediment (838 mg/kg) probably represent material deposited prior to 1980 since there are no chlorinated organics associated with the Hooker Chemical discharge detected. It is also interesting to note that the chromium levels are low (49 mg/kg) in the sediments that predate the 1950s. These data suggest that the deposition of chromium at Station E-9 has been increasing since the 1950s. The greatest flux of chromium to this location has occurred after 1980. This pattern is consistent with a mass of contaminated sediment that is moving out of Tannery Bay into eastern White Lake.

The core sample from E-7 contained no detectable semivolatiles. There was no evidence of the deposition of target organic compounds related to the Koch Chemical NPL Site in this area of White Lake.

Figure 4.6.1
Results of Semivolatiles Analysis on Core Samples from
Stations E-7 and E-9

4.7 References:

Appleby, P. G. and F. Oldfield. 1983. The assessment of 210Pb data from sites with varying sediment accumulation rates. Hydrobiologia 103: 29-35.

Bolattino, C. and R. Fox. 1995. White Lake Area of Concern: 1994 sediment assessment. EPA Technical Report. Great Lakes National Program Office, Chicago.

EPA, 1992. Sediment Classification Methods Compendium. U.S. Environmental Protection Agency. EPA/823/R-92/006.

EPA, 1994. Methods for Measuring the Toxicity and Bioaccumulation of Sediment-Associated Contaminants with Freshwater Invertebrates. U.S. Environmental Protection Agency. EPA/600/R-94/024.

Hassan, S. M. and A. W. Garrison. 1996. Distribution of chromium species between soil and porewater. Chemical. Speciation and Bioavailability. 8:(3/4)85-103.

Horizon Environmental. 1996. Hydrogelogical Investigation Report for Whitehall Leather. March 1996.

Horizon Environmental. 1997. Supplemental Hydrogelogical Investigation Report for Whitehall Leather. February 1997.

Hyland, J. L., L. Balthis, C. T. Hackney, G. McRae, A. H. Ringwood, T. R. Snoots, R. F. Van Dolah, and T. L. Wade. (In Press). Environmental Quality of Estuaries of the Carolinian Province: 1995. Annual Statistical Summary for the 1995 EMAP-Estuaries Demonstration Project in the Carolinian Province. NOAA Techincal Memorandum NOS ORCA 123. NOAA/NOS, Office of Ocean Resources Conservation and Assessment, Silver Spring, MD.

Ingersoll, C. G., P. S. Haverland, E. L. Bruson, T. J. Canfield, F. J. Dwyer, C. E. Henke, N. E. Kemble, D. R. Mount, and R. G. Fox. 1996. Calculation and evaluation of sediment effect concentrations for the amphipod Hyalella azteca and the midge Chironomus riparus. J. Great Lakes Res., 22(3): 602-623.

James, B.R. and R. J. Bartlett. 1983. Behavior of chromium in soils. V. Fate of organically complexed Cr(III) added to soils. J. Environ. Qual. 12:169-172.

Kaczynski, S. E, and R. J. Kiebler. 1994. Hydrophobic C18 bound organic complexes of chromium and their impact on the geochemistry of chromium in natural waters. Environ. Sci. Technol. 28:799-804.

Lung, W. S. 1975. Modeling of Phosphorus Sediment-Water Interactions in White Lake, Michigan. Doctoral Thesis. University of Michigan. Department of Civil Engineering.

Long, E. R., and Morgan, L. G. 1990. The Potential for Biological Effects of Sediment-Sorbed Contaminants Tested in the National Status and Trends Program. NOAA Technical Momorandum NOS OMA 52, Seattle, WA.

Palmer, C. D. and R. W. Puls. 1994. Natural Attenuation of Hexavalent Chromium in Groundwater and Soils. U.S. Environmental Protection Agency. EPA/540/5-94/505.

Persaud, D., R. Jaagumagi, and A. Hayton. 1992. Guidelines for the Protection and Management of Aquatic Sediment Quality in Ontario. ISBN 0-7729-9248-7. Ontario Ministry of the Environment, Toronto, Canada, 23 p.

Robbins, J. A., and L. R. Herche. 1993. Models and uncertanty in 210Pb dating of sediments. Int. Ver. Theor. Angew. Limnol. Verh 25:217-222.

Schelske, C. L. and D. Hodell. 1995. Using carbon isotopes of bulk sedimentary organic matter to reconstruct the history of nutrient loading and eutrophication in Lake Erie. Limnol. Oceanogr. 40:918-929.

Smith, S. L., D. D. MacDonald, K. A. Keenleyside, C. G. Ingersoll, and L. J. Field. 1996. A preliminary evaluation of sediment quality assessment values for freshwater sediments. J. Great Lakes Res., 22(3): 624-638.

Usinger, R. L. 1974. Aquatic Insects of California. University of California Press. Los Angeles, CA. 508 pp.

5.0 Summary

By using a combination of chemistry, toxicological evaluation, ecological analysis, and radiodating, this investigation has defined the ecological effects and the nature and extent of sediment contamination in the Tannery Bay area of eastern White Lake. The sediments in Tannery Bay represent a source of chromium transport for most of the eastern basin of White Lake. The recent deposition of chromium contaminated sediments exceeding 500 mg/kg in down gradient locations shows that export processes are responsible for the movement of this material from Tannery Bay. Arsenic and mercury appear to be less mobile and are retained in the sediments of Tannery Bay. Chromium export from Tannery Bay into White Lake proper will continue as long as the contaminated sediments are influenced by hydrodynamic circulation patterns and wave action.

Chromium stratigraphy in the Tannery Bay region indicates that the top 15-20 cm of sediment are less contaminated (2,000-4,000 mg/kg) than sediment located at >30 cm (>5,000 mg/kg). Radionuclide results suggest that this surface sediment layer is well mixed, however, distinct from the deeper more highly contaminated sediments. Presently this near surface sediment layer (15-20 cm) does not physically mix with the deeper, more contaminated sediment. The 0-20 cm layer is followed by a region (30-80 cm) that contains chromium levels in excess of 20,000 mg/kg. Since the direct discharge of tannery effluent to this area ceased in 1976, evidence of the deposition of sediment with less chromium contamination should be apparent. The lack of a decreasing gradient of chromium concentration in the near surface zone sediments (0-20 cm) suggests that the processes of mixing and resuspension continue to be active in Tannery Bay. In addition, chromium transport to the 0-20 cm sediment zone may also be occuring by other mechanisms including surface runoff of contaminated soils and groundwater advection. The lack of a significant 137Cs horizon in the sediments indicates that groundwater is discharging in this region; however, the linkage with chromium mobility requires further investigation.

The laboratory toxicity evaluation of the Tannery Bay sediments (Ponar samples) found six of eight locations to be toxic to amphipods and two of eight locations to be toxic to midges. The amphipod toxicity was found to be dependent on the depth the sediment. Sediments evaluated below 30 cm exhibited extreme toxicity to amphipods while some survival was observed in the region of 0-30 cm. We were unable to identify the chemical/chemicals responsible for the toxicity observed in the sediments. Amphipod populations did not reflect the laboratory sediment toxicity as Hyalella sp. was found at the same locations that were toxic to the test organisms. This apparent paradox can be explained by examining the natural habitat of these organisms. The native amphipod populations were primarily associated with macrophytic plants and other submerged materials. They did not appear to be associated with the sediments. Similar abundances of chironomids were found at the interior and exterior stations; however, populations of Chironomus sp. were significantly lower in the interior stations. The lower abundances of this genera may reflect a response to toxic chemicals in the sediment since they feed on detrital material. Even though chironomids were found in the Tannery Bay area, a majority of the genera were predators which do not ingest detritus as their primary food source. Finally, mercury bioaccumulation was not observed under laboratory or field conditions.

Chromium concentrations in all locations of Tannery Bay and in five of the six downgradient locations in eastern White Lake exceeded current sediment quality guidelines for probable adverse ecological effects. Most of the Tannery Bay stations exceeded these guidelines by an order of magnitude. Only the background station E-1P had a chromium concentration below the sediment quality guideline that would indicate no adverse effects.

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