Development of California Public Health Goals (PHGs) for chemicals in drinking water.

As part of a program for evaluation of environmental contaminants in drinking water, risk assessments are being conducted to develop Public Health Goals (PHGs) for chemicals in drinking water, based solely on public health considerations. California's Safe Drinking Water Act of 1996 mandated the development of PHGs for over 80 chemicals by 31 December 1999. The law allowed these levels to be set higher or lower than federal maximum contaminant levels (MCLs), including a level of zero if data are insufficient to determine a specific level. The estimated safe levels and toxicological rationale for the first 26 of these chemicals are described here. The chemicals include alachlor, antimony, benzo[a]pyrene, chlordane, copper, cyanide, dalapon, 1,2-dichlorobenzene, 1,4-dichlorobenzene, 2,4-D, diethylhexylphthalate, dinoseb, endothall, ethylbenzene, fluoride, glyphosate, lead, nitrate, nitrite, oxamyl, pentachlorophenol, picloram, trichlorofluoromethane, trichlorotrifluoroethane, uranium and xylene(s). These risk assessments are to be considered by the State of California in revising and developing state MCLs for chemicals in drinking water (which must not exceed federal MCLs). The estimates are also notable for incorporation or consideration of newer guidelines and principles for risk assessment extrapolations.

Potency equivalency factors for some polycyclic aromatic hydrocarbons and polycyclic aromatic hydrocarbon derivatives.

Potency equivalency factors (PEFs) for cancer induction relative to benzo[a]pyrene have been derived for 21 polycyclic aromatic hydrocarbons (PAHs) and PAH derivatives based on a data preference scheme. PEFs have been derived only for PAHs with demonstrated carcinogenicity in bioassays. Cancer potency values and inhalation unit risks are presented for four additional carcinogenic PAHs based on expedited risk assessments conducted for California's Proposition 65. A much larger number of PAHs and PAH derivatives are considered mutagenic or genotoxic and may have limited evidence for carcinogenicity, but these compounds are not considered in this evaluation. New cancer bioassay data and possibly structure-activity analysis may indicate that additional PAHs are carcinogenic. Thus, additional PAHs may be identified as potential human carcinogens when such data become available. However, until that time the PEFs proposed for use in risk assessment were estimated only for PAHs currently classified as carcinogens.

Potential carcinogenicity of chloral hydrate--a review.

Chloral hydrate is commonly used to sedate children for diagnostic or therapeutic procedures. The drug has been extensively used for many years, but there are remarkably few data on its long-term health effects. Concern in this regard is raised by recent studies showing chloral hydrate to be genotoxic, causing chromosome changes and other effects in vivo and in vitro. In addition, chloral hydrate is a reactive metabolite of trichloroethylene, a known carcinogen, and is structurally similar to other carcinogenic intermediates. Two carcinogenicity studies performed using the oral route of administration in mice indicate that the drug is potentially carcinogenic--in one case after a single dose lower than the typical dose used for sedation. Practitioners should be aware of chloral hydrate's genotoxicity and potential carcinogenicity. Discretion in its use seems appropriate until further studies clarify its long term health consequences.

Long-term carcinogenesis studies on 2,3,7,8-tetrachlorodibenzo-p-dioxin and hexachlorodibenzo-p-dioxins.

2,3,7,8-Tetrachlorodibenzo-p-dioxin (TCDD) and 1,2,3,6,7,8- and 1,2,3,7,8,9-hexachlorodibenzo-p-dioxins (HCDDs) are among the most toxic and carcinogenic of "man-made" chemicals. These "dioxins," as well as many of the other polychlorinated dibenzodioxins (PCDDs) and dibenzofuran (PCDFs) derivatives, are chlorinated aromatic compounds which are chemically stable, insoluble in water, and highly soluble in fats and oils. TCDD acts as a complete carcinogen in several species, causing both common and uncommon tumors at multiple sites. It is a highly potent chemical carcinogen in chronic animal studies, producing carcinogenic effects in laboratory animals with doses as low as 0.001 micrograms/kg/day. In rats, TCDD induces neoplasms in the lung, oral/nasal cavities, thyroid and adrenal glands, and liver. In mice, TCDD induces neoplasms in the liver and subcutaneous tissue, thyroid gland, and thymic lymphomas. In hamsters, it induces squamous cell carcinomas of the facial skin. Tumors of the integumentary system are reported after oral (mice and rats), intraperitoneal (hamsters), and dermal (mice) administration. A mixture of HCDDS (defined as the mixture of the 1,2,3,6,7,8- and 1,2,3,7,8,9 isomers used in the NTP experiments) are potent liver carcinogens in mice and rats. Pharmacokinetic studies in laboratory animals indicate that 50-90% of dietary TCDD is absorbed. It concentrates in adipose tissue and the liver. In mammals, the TCDD present in the liver is slowly redistributed and stored in fatty tissue. Elimination of TCDD occurs via excretion of metabolites in the bile and urine and passively through the gut wall. Metabolism is slow: the biological half-life of TCDD varies from weeks (rodents) to years (humans), and is strongly dependent upon the rate of TCDD metabolism. Many of the toxic effects of TCDD, including teratogenicity, may arise by receptor-mediated mechanisms. The induction of cytochrome P-448 and related enzymes by TCDD occurs by such a mechanism, and is related to the binding of TCDD to the Ah receptor. The specific mechanism(s) by which TCDD exerts its carcinogenic effects is unclear: receptor-binding may be part of the story. The role of the Ah receptor has been indicated in a skin promotion assay. The evidence for mutagenicity is inconclusive. TCDD did not induce lethal mutations, chromosomal aberrations, micronuclei or sister chromatid exchanges in rodents treated in vivo, nor was it mutagenic to bacteria, but it did enhance transformation of mouse C3H 10T1/2 cells by N-methyl-N'-nitro-N-nitrosoguanidine and was mutagenic to mouse lymphoma cells.(ABSTRACT TRUNCATED AT 400 WORDS)

Exposure and response to methyl isocyanate: results of a community based survey in Bhopal.

In the two weeks immediately after the Bhopal disaster a community based survey was carried out in a series of eight exposed and two non-exposed clusters of households. The primary concern was the effect of the gas (subsequently identified as methyl isocyanate) on the eyes of the victims but data were also sought on respiratory status and the first symptoms of the exposure. No case of blindness was encountered that could be attributed to the gas. The most frequent symptoms reported were burning of the eyes, coughing, watering of the eyes, and vomiting. Among these, the frequency of cough most closely followed the rate of death in the different clusters. Although much rarer overall, the frequency of reported diarrhoea appeared to bear a stronger relation to death rates. Reports of photophobia and the clinical finding of superficial interpalpebral erosion of the cornea were more frequent where the death rates were lower. This clinical and epidemiological picture is consistent with different effects of the gas at different doses (as estimated from distance from the factory).

Acute toxicity of methyl isocyanate: a preliminary study of the dose response for eye and other effects.

Acute toxic effects of methyl isocyanate in the rat were determined for two hour exposures to concentrations in the range 11 ppm (very slight effect) to 65 ppm (lethality: pulmonary oedema). Changes in the eye, lungs, and behaviour were noted. Eye changes were confined to erosions of the corneal epithelium and were most severe at intermediate levels of exposure. A comparison was made of the effects noted in rats with reported effects on survivors of the Bhopal disaster. Urinary thiocyanate concentrations in exposed rats were found to be reduced relative to control values.

Dechlorination of halocarbons by microsomes and vesicular reconstituted cytochrome P-450 systems under reductive conditions.

A spectrophotometric assay of the reductive dechlorination of halocarbons was developed and used to determine the kinetic characteristics of dechlorination of a range of haloethanes catalysed by microsomes from rat and rabbit liver. Analysis of the typical reaction of hexachloroethane shows that the reaction is catalysed by cytochrome P-450 and results in the formation of olefinic products as well as less chlorinated alkanes: in other respects the reaction resembles that known to occur with carbon tetrachloride. The dechlorination of haloethanes catalysed by a vesicular reconstituted system of cytochrome P-450 enzymes from rabbit liver was also studied and found to be similar to that catalysed by microsomes: both reductase and a phenobarbital inducible form of cytochrome P-450 were essential. There is no substantial dependence of maximum dechlorination rate on compound structure, suggesting that the reduction of substrate is not the rate limiting step in the overall reaction. The main factor in determining the apparent binding constant to the enzyme is the partition coefficient into the lipid membrane, as assessed by calculated log P values.

Microsomal dechlorination of chloroethanes: structure-reactivity relationships.

1. The dechlorination rates of six haloethanes were investigated in vitro, using liver microsomes derived from rats treated with Aroclor 1254. 2. The compounds studied were 1,1-dichloroethane, 1,2-dichloroethane, 1,1,1-trichloroethane, 1,1,2,2-tetrachloroethane, 1,1,1-trifluoro-2-chloroethane and hexachloroethane. 3. Dechlorination kinetics (Km and Vmax) were measured at various substrate concentrations. 4. Electron densities in the molecules for which dechlorination data are available were calculated by the MINDO/3 method. 5. A previously reported correlation between electronic parameters and dechlorination rate was not confirmed, but rather a separate relationship between these parameters for each of three structural classes (RCH2Cl, RCHCl2 and RCCl3) was observed. 6. On the basis of these observations, possible reaction mechanisms and their toxicological implications are discussed.

Cytochrome P-450 and the metabolism of vinyl chloride.

The oxidation of vinyl chloride to non-volatile products is dependent on NADPH and microsomal enzymes. The addition of vinyl chloride to microsomes causes a Type 1 spectra shift, similar to that seen for phenobarbital [11[ which indicates the direct involvement of a cytochrome P-450 species; this difference spectrum is characteristic of substrate binding to this type of enzyme. A glutathione conjugate is probably formed, perhaps via a reactive intermediate.

Benzo(alpha)pyrene effects on mouse epithelial cells in culture.

The effect of benzo (a) pyrene on the growth in culture of 5 mouse epithelial cell strains was examined. These epithelial cells are highly sensitive to the cytotoxic action of benzo (a)-pyrene. In addition, the activity of the benzol (a) pyrene-metabolizing system, aryl hydrocarbon hydroxylase, is low but highly iducible by the carcinogen. As the sensitivity of a cell strain to the cytotoxic action of benjo (a) pyrene decreased, the inudcibility of the hydroxylase also decreased,. However, a strong correlation could not be found between cytotoxicity and the level of uninduced or induced hydroxylase when the values from different cell strains were compared. These experiments suggest that thehydroxylase is important in determining the sensitivity of epithelial cells to the cytotoxic action of benzo (a) pyrene, but other factors may also modulate this sensitivity.