Biodegradation and ecotoxicity of HFCs and HCFCs.

Hydrofluorocarbons (HFCs) and hydrochlorofluorocarbons (HCFCs) are used or developed as substitutes for fully halogenated chlorofluorocarbons. Based on the results of closed-bottle tests, the biodegradation of HFC-32, HCFC-123, HCFC-124, HFC-125, HFC-134a, HCFC-141b, HCFC-225ca, and HCFC-225cb was less than 60% after 28 days and therefore these compounds are considered not readily biodegradable. Standard acute toxicity tests with HCFC-123, HCFC-141b, and HCFC-225ca using algae, water fleas, and fish revealed EC50 values in the range of 17-126 mg/L. EC50 values of HFC-134a ranged between 450-980 mg/L. Fish studies with HCFC-141b and HCFC-225ca revealed bioaccumulation factors of <3 and 15-64, respectively. A study with plants revealed no effect of HCFC-141b on seed germination and growth of wheat (Triticum aestivum), radish (Raphanus sativus), and cress (Lepidium sativum). In conclusion, HFCs and HCFCs are not very toxic to aquatic organisms and terrestrial plants. No evidence for any aerobic biodegradation for most of the HFCs and HCFCs was found.

Bioaccumulation and lack of toxicity of octachlorodibenzofuran (OCDF) and octachlorodibenzo-p-dioxin (OCDD) to early-life stages of zebra fish (Brachydanio rerio).

Previous studies with octachlorodibenzo-p-dioxin (OCDD) and octachlorodibenzofuran (OCDF) in juvenile or adult fish exposed via water revealed no toxicity, despite significant bioaccumulation. With 2,3,7,8-tetrachlorodibenzo-p-dioxin (2,3,7,8-TCDD), the fish early-life stage study has been shown to be the most sensitive test system. Therefore, the effects of OCDD and OCDF on the early-life stages of zebra fish (Brachydanio rerio) were determined during a flow-through test based on a column generator method. No statistically significant effect of OCDD and OCDF on the survival and hatching time of the eggs was found. Furthermore, no effects on survival, weight, general appearance or behaviour of the larvae were observed at the end of the exposure period of 32 days. GC-MS analysis of test solution samples revealed geometric mean measured concentrations of 32 (OCDD) and 34 ng/l (OCDF), respectively. Concentrations in surviving larvae at the end of the study were 61 (OCDD) and 94 (OCDF) micrograms/kg, respectively. These concentrations in zebra fish larvae were several orders of magnitude higher than concentrations in fish collected from the wild. In a review of the available laboratory fish experiments, we found a lack of biomagnification of OCDD and OCDF. We do not expect to find adverse effects of these compounds on the aquatic environment.

Evaluation of the genotoxicity potential and chronic inhalation toxicity of 1,1-dichloro-1-fluoroethane (HCFC-141b).

A battery of in vitro and in vivo tests were conducted on HCFC-141b as a vapour. Bacterial gene mutation assays with Escherichia coli and Salmonella typhimurium were negative in all tester strains. In vitro chromosomal aberration assays were positive on CHO cells but negative on human lymphocytes. Moreover, HCFC-141b was negative in vivo in a mouse micronucleus inhalation assay. On the basis of these data and previously reported genotoxicity testing, HCFC-141b is considered non-genotoxic. Groups of 80 male and 80 female Sprague-Dawley rats were exposed, by inhalation (6 hr/day, 5 days/wk) to vapours of HCFC-141b for 104 wk at target concentrations of 0 (control), 1500, 5000 and 20,000 ppm (increased from 15,000 ppm after 17 wk of exposure). No exposure-related effects of toxicological significance were noted with respect to survival, clinical signs, ophthalmoscopy, haematology, clinical chemistry, urinalysis or organ weight analysis. Reduced food intake and body weight gain were noted in both sexes of the 15,000 ppm group during the first 16 wk; thereafter, body weight gains in all groups were similar although the intergroup differences in body weight remained evident. Reduced food intake persisted in both sexes through wk 52 and in females during the second year of exposure. Treatment-related effects on macroscopic pathology were confined to increased incidences of testicular masses and altered appearance. Microscopic pathology examinations confirmed the testes as the target organ with findings of increased incidences of benign interstitial cell tumours and hyperplasia at 5000 and 20,000 ppm. The no-observable-adverse-effect level (NOAEL) was 1500 ppm. The testicular changes at high exposure levels were considered to be due to a change of the senile hormonal imbalance in geriatric rats and of little significance for the assessment of human health effects.

Health risk assessment of environmental exposure to trichloroethylene.

A review of the animal data showed trichloroethylene (TRI) to be of low acute toxicity. Repeated exposure showed that the target organs were the liver, and to a lesser extent, the kidney. TRI is not mutagenic or only marginally mutagenic. There is no evidence of fetotoxicity or teratogenicity. TRI is judged not to exhibit chronic neurotoxicity. Lifetime bioassays resulted in tumors in both the mouse and the rat. However, because of qualitative and quantitative metabolic differences between rodent and human, no one suitable tumor site can be chosen for human health risk assessment. In addition, of the several epidemiology studies, none has demonstrated a positive association for increased tumor incidence. A review of the health effects in humans shows TRI to be of low acute toxicity and, following chronic high doses, to be hepatotoxic. Environmental exposure to TRI is mainly via the atmosphere, while the contribution from exposure to drinking water and foodstuffs is negligible. The total body burden was calculated as 22 micrograms/day. The safety margin approach based on human health effects showed that TRI levels are well within the safety margin for the human no-observable-effect level (10,000 times lower). The total body burden represents a risk of 1.4 X 10(-5) by linearized multistage modeling. Therefore, by either methodological approach to risk assessment, the environmental occurrence of TRI does not represent a significant health risk to the general population or to the population in areas close to industrial activities.

Health risk assessment of environmental exposure to 1,1,1-trichloroethane.

In 1986 a survey was published by CEFIC on the occurrence of chlorinated solvents in ambient air, in surface water, and in ground water. The present article concentrates on 1,1,1-trichloroethane (1,1,1-T), and puts into perspective the environmental occurrence and the toxicity. Critical toxicological data are briefly discussed. As no evidence of a carcinogenic effect of 1,1,1-T is apparent, the no-adverse-effect levels in chronic inhalation exposure in rats (875 ppm) and mice (1500 ppm) form the basis for the estimation of potential risk to human health. Environmental exposure to 1,1,1-T is mainly via the atmosphere (120 micrograms/day); the contributions of drinking water (2 micrograms/day) and food (3 micrograms/kg) are negligible. Safety margins are calculated by comparing the no-adverse-effect levels in rat and mouse studies with the total body burden. Safety margins are also calculated after converting no-adverse-effect levels into estimated internal dose levels by physiologically based pharmacokinetic modeling. Safety margins vary with the starting point, but are of the order of 10(5) for the general population and more than 10(4) for the population close to industrial activities. It may be concluded that the risk of a potential health effect resulting from environmental exposure to 1,1,1-trichloroethane is negligible.