Hazardous waste sites monitoring

Turpin, R., K. Vora, J. Singh, A. Eissler, and D. Stranbergh. On-Site Air Monitoring Classification by the Use of a Two-Stage Collection Tube," Management of Uncontrolled Hazardous Waste Sites Proceedings, Hazardous Materials Control Research Institute, Washington, D.C., 1984. 

Only qualified individuals should be allowed to develop air monitoring strategies. In addition, only trained and qualified field personnel should operate sereening equipment and be allowed to interpret results. For many sites, the results obtained from direet reading instruments ean help determine a variety of important faetors on a hazardous waste site. These faetors inelude ... 

Reliable monitoring data for the levels of endosulfan in contaminated media at hazardous waste sites are needed. This information could be used in combinahon with the known body burdens of endosulfan to assess the potential risk of adverse health effects in populations living in the vicinity of hazardous waste sites. 

Exposure Levels in Humans. This information is necessary for assessing the need to conduct health studies on these populations. Trichloroethylene has been detected in human body fluids such as blood (Brugnone et al. 1994 Skender et al. 1994) and breast milk (Pellizzari et al. 1982). Most of the monitoring data have come from occupational studies of specific worker populations exposed to trichloroethylene. More information on exposure levels for populations living in the vicinity of hazardous waste sites is needed for estimating human exposure. 

Reliable and more recent monitoring data of chromium in air, water, and food, with emphasis on chromium levels in tissues and body fluids of animals living near hazardous waste sites... 

Exposure Levels in Humans. Hexachloroethane has not been detected in human tissues as a result of exposure to this chemical from environmental media. Biological monitoring data were not located for populations surrounding hazardous waste sites. Hexachloroethane has been detected in the plasma of workers at concentrations of 7.3 6 pg/L, despite the use of protective equipment including disposable overalls and compressed-air-fed visors or full-facepiece masks with filters (Selden et al. 1994). Because of protective equipment, exposure concentrations could not be related to plasma levels of hexachloroethane. 

Exposure Levels in Environmental Media. Reliable monitoring data for the levels of di- -octylphthalate in contaminated media at hazardous waste sites are needed so that the information obtained on levels of di-ra-octylphthalate in the environment can be used in combination with the known body burden of di-w-octylphthalate to assess the potential risk of adverse health effects in populations living in the vicinity of hazardous waste sites. Di-u-octylphthalate has been detected in ambient air, rain, surface water, groundwater, and sediment. However, as a result of the confusion about the nomenclature for octylphthalate esters, much of the historical monitoring data available actually pertain to the branched isomer, di(2-ethylhexyl)phthalate (Vista Chemical 1992). Therefore, little current information specific to the /1-octyl isomer is available regarding concentrations of the compound in foods, drinking water, and environmental media, particularly with respect to media at hazardous waste sites. The lack of monitoring data precludes the estimation of human exposure via intake of or contact with contaminated media. 

Soil monitoring data in the peer reviewed literature could not be located. It can be predicted that chloroform contamination occurs at hazardous waste sites where chloroform-containing leachate moves through the soil to groundwater. An explanation of the lack of data results from the fact that any chloroform in the soil is expected to either rapidly volatilize or leach. Laboratory studies using a variety of different soil types document the effectiveness of volatilization in removing chloroform from soils (Park et al. 1988). 

Exposure Levels in Humans. Heptachlor epoxide has been detected in human blood, tissues (including adipose tissue), and breast milk (Al-Omar et al. 1986 Holt et al. 1986 Larsen et al. 1971 Savage et al. 1981). The presence of heptachlor epoxide is used as an indicator of exposure to heptachlor. Current monitoring studies of heptachlor epoxide in these tissues and fluids would be helpful in assessing the extent to which populations, particularly in the vicinity of hazardous waste sites, have been exposed to heptachlor. 

Methods for Determining Parent Compound and Degradation Products in Environmental Media. While analytical methods appear to be available for the analysis of 1,2-diphenylhydrazine, no methods were found for the preservation of 1,2-diphenylhydrazine in ambient air, water, or soil samples. Such methods would allow the development and analysis of a monitoring program designed to better assess the concentrations of 1,2-diphenylhydrazine in and around hazardous waste sites. 

Renal Effects. No studies were located regarding renal effects in humans after exposure to 3,3 -dichlorobenzidine by any route. No effects to the kidneys or urinaiy parameters monitored were observed in dogs exposed to 10.4 mg/kg/day for up to 7 years (Stula et al. 1978). Based on these data, it is unlikely that kidney effects will occm in humans exposed to 3,3 -dichlorobenzidine at levels found at hazardous waste sites. 

Effect. There are no specific disease states in humans or animals that have been associated with exposure to 3,3 -dichlorobenzidine. Hemoglobin adducts have been isolated from the blood of 3,3 -dichlorobenzidine-treated animals (Bimer et al. 1990 Joppich-Kuhn et al. 1997). It is not known what relationship exists between adduct levels in the blood and 3,3 -dichlorobenzidine toxicity. Further research in animal models is needed to determine if these adducts could be correlated with effects of 3,3 -dichlorobenzidine exposure. Further studies to identify more sensitive toxic effects (noncancer) that are specific for 3,3 -dichlorobenzidine would be useful in monitoring effects in people living near hazardous waste sites containing 3,3 -dichlorobenzidine. 

In general, cresols will degrade in surface waters very rapidly. However, cresols may persist in groundwater due to a lack of microbes and/or anaerobic conditions. Cresols are largely released to groundwater via landfills and hazardous waste sites. Tables 5-2a through 5-2e include monitoring data for these sources. 

Hutchins et al. 1980 Oliveira and Sitar 1985 Ram et al. 1985 Sawhney and Kozlowski 1984 Stuermer et al. 1982 Weber and Matsumota 1987) only (sources of groundwater contamination include hazardous waste sites). Data describing the exposure levels in air and surface water are lacking. It is not clear whether monitoring studies were not performed, or were not found. Quantified levels of cresols in food are also lacking. Estimates of human intake are not available. 

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