Proposed changes in the classification of carcinogenic chemicals in the work area

Update: Mode of action (MOA) for liver tumors induced by oral exposure to 1,4-dioxane

Previous work has shown that the weight of evidence supports the hypothesis that 1,4-dioxane causes liver tumors in rodents through cytotoxicity and subsequent regenerative hyperplasia. Questions regarding a lack of concordant findings for this mode of action (MOA) in mice have not been resolved, however. In the current work, a reanalysis of data from two chronic mouse cancer bioassays on 1,4-dioxane, one 13-week mouse study, seven rat cancer bioassays, coupled with other data such as 1,4-dioxane's negative mutagenicity, its lack of up-regulated DNA repair, and the appearance of liver tumors with a high background incidence, support the conclusion that rodent liver tumors, including those in mice, are evoked by a regenerative hyperplasia MOA. The initiating event for this MOA is metabolic saturation of 1,4-dioxane. Above metabolic saturation, higher doses of the parent compound cause an ever increasing toxicity in the rodent liver as evidenced by higher blood levels of enzymes indicative of liver cell damage and associated histopathology that occurs in a dose and time related manner. Importantly, alternative modes of action can be excluded. The observed liver toxicity has a threshold in the dose scale at or below levels that saturate metabolism, and generally in the range of 9.6-42 mg/kg-day for rats and 57 to 66 mg/kg-day for mice. It follows that threshold approaches to the assessment of this chemical's toxicity are supported by the non-mutagenic, metabolic saturation kinetics, and cytotoxicity-generated regenerative repair information available for 1,4-dioxane promoted rodent liver tumors.

Benzene and its methyl-derivatives: Derivation of maximum exposure levels in automobiles

Automobile drivers are exposed to several organic hydrocarbons. Concentrations measured in passenger compartments have been reported to range between 13 and 560 microg/m(3) for benzene, 33-258 microg/m(3) for toluene, 20-250 microg/m(3) for xylene (mixed isomers) and 3-23 microg/m(3) for trimethylbenzene (mixed isomers). These aromatic hydrocarbons are emitted from gasoline and from materials inside a car. In the present study we evaluated, whether these exposures pose a potential risk to the health of drivers. Therefore, we derived maximum exposure levels inside cars for chronic (ELIA(chronic)) and short-term (STELIA) exposure. The lowest ELIA's(chronic) for benzene, toluene, xylene and trimethylbenzene were 0.083, 1.2, 8.8 and 0.31 mg/m(3), respectively. The respective STELIA's were 16, 30, 29 and 25 mg/m(3). Obviously concentrations of toluene, xylene and trimethylbenzene inside cars do not exceed their individual STELIA's. In contrast, benzene seems to be problematic, since concentrations inside cars amount up to 0.56 mg/m(3), which exceeds the ELIA(chronic) derived for benzene. This should not be underestimated, since benzene is a genotoxic carcinogen that probably acts by non-threshold mechanisms. In conclusion, concentrations of toluene, xylene and trimethylbenzene usually observed inside cars are unlikely to pose a risk to the health of drivers. A systematic toxicological evaluation of the risk associated with benzene exposure in cars seems to be necessary.

Research needs to improve risk assessment of fiber toxicity

Risk characterization of exposure to toxic compounds requires information on the intrinsic toxic properties, including toxic mechanism and toxicokinetics, on dose response at the most critical targets for identification of the NOEL or for extrapolation from high to low dose, and on human exposure. Abundant information is available on the intrinsic properties of MMMF, on the three D's (dose, dimension, durability) and on the toxic mechanisms. However, only a few of these studies provide information on the dose response of the effects or of the mechanisms investigated. Moreover, in many cases single high doses exceeding the MTD have been applied and are difficult to interpret for lower exposure scenarios. Risk characterization is further hampered by the still open question whether MMMF are directly genotoxic or induce secondary genotoxicity via inflammation. Finally, there is disagreement about the relevance of animal studies on MMMF for humans and thus about the most rational extrapolation of the dose response of toxic effects observed in animals to man. These deficits are briefly described and discussed from a toxicological point of view.

An updated evaluation of the carcinogenic potential of 1,4-dioxane

This paper presents a critical review of the information pertaining to the potential carcinogenicity of 1,4-dioxane. The primary target organs for cancer via the oral route are the liver and the nasal cavity, however, the relevance of nasal cavity tumors to human exposures has been questioned. Liver tumors were accompanied by degenerative changes and appear only to occur at high doses where clearance mechanisms are saturated and liver toxicity is significant. Genetic toxicity data suggests that 1,4-dioxane is a very weak genotoxin. An increase in hepatocyte cell proliferation was reported and 1,4-dioxane was shown to act as a tumor promoter in rat liver and mouse skin carcinogenicity assays. Two reports are available from the literature regarding physiologically based pharmacokinetic (PBPK) modeling approaches to assess the risk of liver cancer for 1,4-dioxane. A comparison of cancer risk estimates from linear and nonlinear models in the presence or absence of PBPK modeling suggests that USEPAs current cancer slope factor significantly overestimates the potential cancer risk from 1,4-dioxane. This critical review of the scientific literature indicates that a formal reevaluation of the carcinogenic potency of 1,4-dioxane is warranted.

Variation of biological responses to different respirable quartz flours determined by a vector model

BACKGROUND

The hypothesis of widely differing lung damage due to commonly used types of quartz was studied in 16 samples of respirable quartzes (> 99% silica) from sites of the European quartz industry, using an in vitro test, the vector model. Two samples with high and 2 with low biological activities were identified and subsequently examined for their in vivo lung toxicity (inflammation, fibrosis, genotoxicity) and surface characteristics. Alveolar macrophages (AM) are considered the target cells of primary dust effects. The vector model mimics some of the elemental dust cell effects such as cell toxicity, effects on the metabolism and stimulatory effects, e.g., TNF alpha and dust-induced ROS secretion.

METHODS

Doses of 15, 30, 60 and 120 microg dust per 10(6) AM were used together with the control dusts (quartz DQ12 and corundum). Testing parameters were LDH, glucuronidase, PMA forced ROS release, TNF alpha and dust induced ROS secretion. The main criterion for the selection of low or high activity samples was the secretion of TNF alpha.

RESULTS

(i) Apart from quartz samples with an activity close to that of DQ12, one also finds examples with a very low activity. (ii) In comparison particular parameters are linked with a specific dose response relationship and different dose points for the leveling off of the effects. The levels of TNF alpha represent a conspicuously broad response pattern; some samples induce secretion at the lowest dose and others are not active even at the highest dose investigated at already apparent toxicity. (iii) Regarding various parameters the dust samples led to distinct dose response profiles considered as vectors. The current study indicates that within the particle type "quartz fine dust" varying harmful doses and different elements of damage must be present. (iv) The lung damage of the subchronic animal assay coincides with in vitro tests thus confirming the concept of the vector model.

CONCLUSION

Threshold effects in the range of 15 - > or = 120 microg can be demonstrated for the discriminant vector TNF alpha, i.e. over 4 steps of dose doubling. These studies show very toxic quartzes but also quartzes of low biological activity comparable to corundum.

Using carcinogenic potency ranking to assign air contaminants to emission classes

Carcinogenic air contaminants are assigned to emission classes with different emission limits on the basis of their inhalation carcinogenic potency within the revised form of the German First General Administrative Regulation Pertaining to the Federal Emission Control Law (Technical Instructions on Air Quality Control-TA Luft). Accordingly, compounds with high carcinogenic potency are regulated more strictly than less potent substances. The data on carcinogenic properties are heterogeneous. Twenty-five substances or substance groups have been scrutinized and a procedure has been developed to rank these chemicals according to their carcinogenic potency. For 14 substances well-founded unit risk estimates were available to allow assignment of these air contaminants to emission classes. Unit risk estimates for bromoethane, 2-butanone oxime, and o-toluidine were derived using the ED(10)/LED(10) method based on animal studies. For several substances no qualified unit risk estimates or carcinogenicity studies were available to estimate carcinogenic potency after inhalation. Carcinogenic potency of these substances was approximated using two simple methods, T25 and CELmin.

Procedures for health risk assessment in Europe

This report compares cancer classification systems, health risk assessment approaches, and procedures used for establishing occupational exposure limits (OELs), in various European countries and scientific organizations. The objectives were to highlight and compare key aspects of these processes and to identify the basis for differences in cancer classifications and OELs between various scientific organizations and countries. Differences in cancer classification exist in part due to differences in the ultimate purpose of classification and to the relative importance of different types of data (i.e., animal vs human data, mechanistic data, and data from benign vs malignant tumors). In general, the groups surveyed tend to agree on classification of chemicals with good evidence of carcinogenicity in humans, and agree less on classification of chemicals with positive evidence in animals and inadequate or limited evidence in humans. Most entities surveyed distinguish between genotoxic and nongenotoxic chemicals when conducting risk assessments. Although the risk assessment approach used for nongenotoxic chemicals is fairly similar among groups, risk assessment approaches for genotoxic carcinogens vary widely. In addition to risk assessment approaches, other factors which can affect OELs include selection of the critical effect, use of health-based vs technology-based exposure limits, and consideration of technological feasibility and socioeconomic factors.

Formation of DNA adducts and induction of mutagenic effects in rats following 4 weeks inhalation exposure to ethylene oxide as a basis for cancer risk assessment

Ethylene oxide (EO) is mutagenic in various in vitro and in vivo test systems and carcinogenic in rodents. EO forms different adducts upon reaction with DNA, N7-(2-hydroxyethyl)guanine (N7-HEG) being the main adduct. The major objectives of this study were: (a) to determine the formation and persistence of N7-HEG adducts in liver DNA of adult male rats exposed to 0, 50, 100 and 200 ppm by inhalation (4 weeks, 5 days/week, 6 h/day) and (b) to assess dose-response relationships for Hprt gene mutations and various types of chromosomal changes in splenic lymphocytes.N7-HEG adducts were measured 5, 21, 35 and 49 days after cessation of exposure. By extrapolation, the mean concentrations of N7-HEG immediately after cessation of exposure ('day 0') to 50, 100 and 200 ppm were calculated as 310, 558 and 1202 adducts/10(8) nucleotides, respectively, while the mean concentration in control rats was 2.6 adducts/10(8) nucleotides. At 49 days, N7-HEG values had returned close to background levels. The mean levels of N-(2-hydroxyethylvaline) adducts in haemoglobin were also determined and amounted 61.7, 114 and 247 nmol/g globin, respectively. Statistically significant linear relationships were found between mean N7-HEG levels ('day 0') and Hprt mutant frequencies at expression times 21/22 and 49/50 days and between mean N7-HEG ('day 0') and sister-chromatid exchanges (SCEs) or high frequency cells (HFC) measured 5 days post-exposure. At day 21 post-exposure, SCEs and HFCs in-part persisted and were significantly correlated with persistent N7-HEG adducts. No statistically significant dose effect relationships were observed for induction of micronuclei, nor for chromosome breaks or translocations. In conclusion, this study indicates that following sub-chronic exposure, EO is only weakly mutagenic in adult rats. Using the data of this study to predict cancer risk in man resulting from low level EO exposures in conjunction with other published data, i.e., those on (a) genotoxic effects of EO in humans and rats, (b) DNA binding of other carcinogens, (c) natural background DNA binding and (d) genotoxic potency of low energy transfer (LET) radiation, it is not expected that long term occupational exposure to airborne concentrations of EO at or below 1 ppm EO produces an unacceptable increased risk in man.