The relationship between microbial community structure and functional stability, tested experimentally in an upland pasture soil

Soil collected from an upland pasture was manipulated experimentally in ways shown previously to alter microbial community structure. One set of soil was subjected to chloroform fumigation for 0, 0.5, 2, or 24 h and the other was sterilised by gamma-irradiation and inoculated with a 10(-2), 10(-4), 10(-6), or 10(-8) dilution of a soil suspension prepared from unsterilized soil. Following incubation for 8 months, to allow for the stabilization of microbial biomass and activity, the resulting microbial community structure (determined by PCR-DGGE of bacterial specific amplification products of total soil DNA) was assessed. In addition, the functional stability (defined here as the resistance and resilience of short-term decomposition of plant residues to a transient heat or a persistent copper perturbation) was determined. Changes in the active bacterial population following perturbation (determined by RT-PCR-DGGE of total soil RNA) were also monitored. The manipulations resulted in distinct shifts in microbial community structure as shown by PCR-DGGE profiles, but no significant decreases in the number of bands. These shifts in microbial community structure were associated with a reduction in functional stability. The clear correlation between altered microbial community structure and functional stability observed in this upland pasture soil was not evident when the same protocols were applied to soils in other studies. RT-PCR-DGGE profiles only detected a shift in the active bacterial population following heat, but not copper, perturbation. We conclude that the functional stability of decomposition is related to specific components of the microbial community.

Biologically motivated computational modeling of chloroform cytolethality and regenerative cellular proliferation

Chloroform is a nongenotoxic-cytotoxic carcinogen in rodents. As such, events related to cytotoxicity are the driving force for cancer induction. In this paper we extended an existing physiologically based pharmacokinetic (PBPK) model for chloroform to describe a plausible mechanism linking the hepatic metabolism of chloroform to hepatocellular killing and regenerative proliferation. The key aspects of this mechanism are (1) the production of damage at a rate proportional to the rate of metabolism predicted by the PBPK model, (2) the saturable repair of the damage, (3) the stimulation of the cell death rate by damage, and (4) the stimulation of the cell division rate as a function of the difference between the control and exposed numbers of cells. This extension allows the simulation of the labeling index and comparison with labeling index data. Data from a previously published chloroform-inhalation study with female B6C3F1 mice that determined cytolethality and regenerative cellular proliferation following exposures of varying concentrations and exposure durations were used for model calibration. Both threshold and low-dose linear linkages between chloroform-induced damage and cell death rate provided visually good fits to the labeling index data after formal optimization of the adjustable parameters, and there was no statistical difference between the fits of the two models to the data. Biologically motivated computational modeling of chloroform-induced cytolethality and regenerative proliferation is a necessary step in the quantitative evaluation of the hypothesis that chloroform-stimulated cell proliferation predicts the rodent tumor response.

Tissue repair plays pivotal role in final outcome of liver injury following chloroform and allyl alcohol binary mixture

The objective of this study was to evaluate the interaction profile of chloroform (CHCl(3))+allyl alcohol (AA) binary mixture (BM)-induced acute hepatotoxic response. Plasma alanine aminotransferase (ALT) was measured to assess liver injury, and 3H-thymidine (3H-T) incorporation into hepatonuclear DNA was measured as an index of liver regeneration over a time course of 0-72 h. Male Sprague-Dawley (S-D) rats received single ip injection of 5-fold dose range of CHCl(3) (74, 185 and 370 mg/kg) in corn oil (maximum 0.5 ml/kg) and 7-fold dose range of AA (5, 20 and 35 mg/kg) in distilled water simultaneously. The doses for BM were selected from individual toxicity studies of CHCl(3) alone [Int. J. Toxicol. 22 (2003) 25], and AA alone [Reg. Pharmacol. Toxicol. 19 (1999) 165]. Since the highest dose of each treatment (CHCl(3)- 740 and AA- 50 mg/kg) yielded mortality due to the suppressed tissue repair followed by liver failure, this dose was omitted for BM. The levels of CHCl(3) (30-360 min) and AA (5-60 min) were quantified in blood and liver by gas chromatography (GC). The liver injury was more than additive after BM compared to CHCl(3) alone or AA alone at highest dose combination (370+35 mg/kg), which peaked at 24 h. The augmented liver injury observed with BM was consistent with the quantitation data. Though the liver injury was higher, the greater stimulation of tissue repair kept injury from progressing, and rescued the rats from hepatic failure and death. At lower dose combinations, the liver injury was no more than additive. Results of the present study suggest that liver tissue repair, in which liver tissue lost to injury is promptly replaced, plays a pivotal role in the final outcome of liver injury after exposure to BM of CHCl(3) and AA.

Chloroform, carbon tetrachloride and glutathione depletion induce secondary genotoxicity in liver cells via oxidative stress

Chemical carcinogens are generally classified as genotoxic or non-genotoxic. However, weak genotoxicity at high concentrations is sometimes observed and interpretation is often problematic. In addition, certain rodent carcinogens exert their effects at doses associated with cytotoxicity and compensatory hyperplasia may be a contributing factor to tumourogenesis. We hypothesise that certain substances, at high concentrations, can induce an oxidative stress via the depletion of glutathione (GSH) and other antioxidant defences and that this may lead to indirect genotoxicity, that could contribute to carcinogenicity. In support of this, human HepG2 cells treated with buthionine sulphoximine (BSO) to deplete GSH, exhibited DNA strand breaks alongside elevated 8-oxodeoxyguanosine (8-oxodG) and malondialdehyde deoxyguanosine (M(1)dG) adducts under conditions associated with lipid peroxidation. Chloroform and carbon tetrachloride are rodent carcinogens with characteristics as described above. In female rat hepatocytes, chloroform treatment resulted in a small dose-dependent increase in M(1)dG adducts (4 mM and above), DNA strand breakage (8 mM and above) and lipid peroxidation, in the absence of any associated increase in DNA oxidation. GSH depletion only occurred in association with cytotoxicity (20 mM; lactate dehydrogenase release). Alongside lipid peroxidation, carbon tetrachloride (1 and 4 mM) produced a small elevation in M(1)dG adducts and DNA strand breaks and increases in 8-oxodG were observed at the threshold of, and concomitant with, cytotoxicity (4 mM). These effects may contribute to high dose genotoxicity and carcinogenicity. Non-linearity in the dose response is expected on the basis of depletion of antioxidants, and therefore, a pragmatic threshold for biologically relevant responses should exist.

Analysis of preneoplastic and neoplastic renal lesions in Tsc2 mutant Long-Evans (Eker) rats following exposure to a mixture of drinking water disinfection by-products

Disinfection of surface water for human consumption results in the generation of a complex mixture of chemicals in potable water. Cancer risk assessment methodology assumes additivity of carcinogenic effects in the regulation of mixtures. A rodent model of hereditary renal cancer was used to investigate the carcinogenic response to a mixture of drinking water disinfection by-products (DBPs). Rats carrying a mutation in the Tsc2 tumor suppressor gene (Eker rats) readily develop renal preneoplastic and neoplastic lesions, and are highly susceptible to the effects of renal carcinogens. Male and female Eker rats were exposed via drinking water to individual or a mixture of DBPs for 4 or 10 months. Potassium bromate, 3-chloro-4-(dichloromethyl)-5-hydroxy-2(5H)-furanone (MX), chloroform, and bromodichloromethane were administered at low concentrations of 0.02, 0.005, 0.4 and 0.07 g/l, respectively, and high concentrations of 0.4, 0.07, 1.8 and 0.7 g/l, respectively. Low and high dose mixture solutions were comprised of all four chemicals at either low concentrations or high concentrations, respectively, Following necropsy, each kidney was examined microscopically for preneoplastic lesions (atypical tubules and hyperplasias) and tumors. While some of the mixture responses observed in male rats did fall within the range expected for an additive response, especially at the high dose, predominantly antagonistic effects on renal lesions were observed in response to the low dose mixture in male rats and the high dose mixture in female rats. These data suggest that current default risk assessments assuming additivity may overstate the cancer risk associated with exposure to mixtures of DBPs at low concentrations.

Effect of a chemical mixture on dermal penetration of arsenic and nickel in male pig in vitro

The effect of a chemical mixture on the dermal penetration of arsenic or nickel was assessed by applying arsenic-73 or nickel-63 alone or with the chemical mixture to dermatomed male pig skin samples in flow-through diffusion cells. The chemical mixture consisted of chloroform, phenanthrene, and toluene for arsenic penetration studies and phenol, toluene, and trichloroethylene (TCE) for nickel studies. These are predominant chemicals found at hazardous waste sites. Arsenic and nickel bind to skin after dermal exposure. Total penetration of arsenic and nickel in the chemical mixture were significantly increased by 33% and 20% compared to arsenic and nickel alone, respectively. While more radioactivity penetrated skin with chemical treatment than metal alone, significantly less radioactivity was loosely adsorbed to skin and could be easily washed off from the skin surface with soap and water. The results of this study indicate that the potential health risk from dermal exposure to arsenic or nickel is enhanced if other chemicals are present.

Late administration of COX-2 inhibitors minimize hepatic necrosis in chloroform induced liver injury

Our previous studies have described the protective effects of hepatoprotective agents against liver injury elicited by chloroform even when given 24 h after the toxicant, at a time when the liver injury is taking place and rapidly developing. However, the mechanisms involved in this protection remain unknown. The cytoprotective mechanism of these hepatoprotectants such as DMSO, may be due to a dramatic shift in the production of prostaglandins that are responsible for controlling the degree of inflammatory response that can affect blood flow in the liver. In this study, NS-398, a specific COX-2 inhibitor, and indomethacin, a COX-1 and COX-2 inhibitor, were administered 24 h after chloroform dosing to determine their effect on liver injury in Sprague-Dawley rats. The extent of necrosis was evaluated by H&E staining, while injury to hepatocytes was evaluated by measuring plasma levels of alanine transaminase (ALT). Both COX inhibitors, indomethacin and NS-398, prevented an increase in (ALT) at 48 h after initial toxicant insult and attenuated further liver necrosis. No changes in cellular proliferative activity occurred in all the treatment groups, which indicates that protection from the Cyclooxygenase (COX) inhibitors did not have an effect on regeneration of cells at 32 and 48 h. These results indicate COX inhibitors provide a significant protective effect on liver cells against CHCl(3) injury and may provide further insight into therapeutic interventions against hepatotoxicants.

Effect of inhaled industrial chemicals on systemic and local immune response

Using immunotoxic functional tests, namely IgM response to sheep red blood cells (SRBCs) and interferon-gamma (IFN-gamma) production, this study simultaneously evaluated the effects of inhaled chloroform (10, 20, and 50 ppm), carbon tetrachloride (100, 200, and 300 ppm), 1,1-dichloroethylene (5, 10, and 15 ppm), and styrene (100, 200, and 300 ppm) on the systemic (spleen) and local (lung-associated lymph nodes) immune response. At least one concentration of all the chemicals studied provoked a statistically significant increase in IgM response in the lymph nodes compared with the controls, as expressed by the number of plaque-forming cells (PFCs), whereas only the highest concentration of 1,1-dichloroethylene provoked an increase in the number of PFCs statistically different from the controls in the case of the spleens. The release of IFN-gamma in the lymph node cell cultures of the exposed mice exceeded that of the controls by more than 600%, whereas the release of IFN-gamma in the spleen cell cultures of the exposed mice was moderately different from the controls. It would appear from these results that the lung-associated lymph nodes are sensitive targets for chemical inhalation and that the results of systemic tests in the spleen may not mirror local immune response dysfunction. For risk assessment of inhaled chemicals, it is therefore important to take the local immunotoxic effects into consideration, in particular immunostimulation which may be involved in the rise in allergic diseases in industrialised countries.

Comparison of cancer risk estimates based on a variety of risk assessment methodologies

The EPA guidelines recommend a benchmark dose as a point of departure (PoD) for low-dose cancer risk assessment. Generally the PoD is the lower 95% confidence limit on the dose estimated to produce an extra lifetime cancer risk of 10% (LTD(10)). Due to the relatively narrow range of doses in two-year bioassays and the limited range of statistically significant tumor incidence rates, the estimate of the LTD(10) is constrained to a relatively narrow range of values. Because of this constraint, simple, quick estimates of the LTD(10) can be readily obtained for hundreds of rodent carcinogens from the Carcinogenic Potency Database (CPDB) of Gold et al. Three estimation procedures for LTD(10) are described, using increasing information from the CPDB: (A) based on only the maximum tolerated dose (the highest dose tested); (B) based on the TD(50); and (C) based on the TD(50) and its lower 99% confidence limit. As expected, results indicate overall similarity of the LTD(10) estimates and the value of using additional information. For Method (C) the estimator based on the [[(TD(50))(0.36) x (LoConf)(0.64)]/6.6] is generally similar to the estimator based on the one-hit model or multistage model LTD(10). This simple estimate of the LTD(10) is applicable for both linear and curved dose responses with high or low background tumor rates, and whether the confidence limits on the TD(50) are wide or tight. The EPA guidelines provide for a margin of exposure approach if data are sufficient to support a nonlinear dose-response. The reference dose for cancer for a nonlinear dose-response curve based on a 10,000-fold uncertainty (safety) factor from the LTD(10), i.e., the LTD(10)/10,000, is mathematically equivalent to the value for a linear extrapolation from the LTD(10) to the dose corresponding to a cancer risk of <10(-5) (LTD(10)/10,000). The cancer risk at <10(-5) obtained by using the q(1)(*) from the multistage model, is similar to LTD(10)/10,000. For a nonlinear case, an uncertainty factor of less than 10,000 is likely to be used, which would result in a higher (less stringent) acceptable exposure level.

Extent and timeliness of tissue repair determines the dose-related hepatotoxicity of chloroform

As a part of mixture toxicity studies, the objective of the present investigation was to validate the hypothesis that the rate and extent of liver tissue repair response to a given dose determines the end result of toxicity (death or recovery), regardless of the mechanisms by which injury is inflicted, using a well-known environmental pollutant, chloroform (CHCl(3)). In future, the data will be used to compare with the results of mixtures containing CHCl(3) to aid in characterizing the safety of chemical mixtures and to construct a physiologically based pharmacokinetic (PBPK) model for dose, route, and species extrapolation. Hepatotoxicity and tissue repair were measured in male Sprague-Dawley rats (S-D) receiving a 10-fold dose range of CHCl(3) (74, 185, 370, and 740 mg/kg, IP) during a time course of 0 to 96 hours. Liver injury, as assessed by plasma alanine aminotransferase (ALT) and sorbitol dehydrogenase (SDH) elevation, increased with dose over the 10-fold dose range. Because CHCl(3) is also known to cause kidney damage, blood urea nitrogen (BUN) and creatinine were measured to evaluate the kidney injury. With doses up to 370 mg/kg, liver injury increased in a dose-related fashion, which peaked at 24 hours and returned to normal after 48 hours, whereas at highest dose (740 mg/kg), the injury was progressive resulting in 90% mortality. Blood and liver CHCl(3) levels were quantified using gas chromatography (GC) over a time course of 30 to 360 minutes. The dose-related increase in the blood and liver CHCl(3) levels were consistent with dose-dependent liver injury. Tissue regeneration response, as measured by [(3)H]-thymidine incorporation into hepatocellular nuclear DNA peaked at 36 hours in rats treated with the lower two doses of CHCl(3) (74 and 185 mg/kg). Further increase in CHCl(3) dose to 370 mg/kg resulted in an earlier increase in [(3)H]-thymidine incorporation at 24 hours, which peaked at 36 hours. However, at the highest dose of CHCl(3) (740 mg/kg), tissue repair was delayed and attenuated, allowing for unrestrained progression of liver injury. The kidney injury markers after CHCl(3) administration were not different from controls. These results support the concept that in addition to the magnitude of tissue repair response, the time at which this response occurs is critical in restraining the progression of injury. Measuring tissue repair and injury as simultaneous biological responses to toxic agents might increase the usefulness of dose-response paradigms in predictive toxicology and risk assessment. Although the dosimetry of the present study was well beyond the environmental exposure levels of CHCl(3), a PBPK model will be developed in future based upon these data to evaluate the effects at environmental levels.

What to do at low doses: a bounding approach for economic analysis

To quantify the health benefits of environmental policies, economists generally require estimates of the reduced probability of illness or death. For policies that reduce exposure to carcinogenic substances, these estimates traditionally have been obtained through the linear extrapolation of experimental dose-response data to low-exposure scenarios as described in the U.S. Environmental Protection Agency's Guidelines for Carcinogen Risk Assessment (1986). In response to evolving scientific knowledge, EPA proposed revisions to the guidelines in 1996. Under the proposed revisions, dose-response relationships would not be estimated for carcinogens thought to exhibit nonlinear modes of action. Such a change in cancer-risk assessment methods and outputs will likely have serious consequences for how benefit-cost analyses of policies aimed at reducing cancer risks are conducted. Any tendency for reduced quantification of effects in environmental risk assessments, such as those contemplated in the revisions to EPA's cancer-risk assessment guidelines, impedes the ability of economic analysts to respond to increasing calls for benefit-cost analysis. This article examines the implications for benefit-cost analysis of carcinogenic exposures of the proposed changes to the 1986 Guidelines and proposes an approach for bounding dose-response relationships when no biologically based models are available. In spite of the more limited quantitative information provided in a carcinogen risk assessment under the proposed revisions to the guidelines, we argue that reasonable bounds on dose-response relationships can be estimated for low-level exposures to nonlinear carcinogens. This approach yields estimates of reduced illness for use in a benefit-cost analysis while incorporating evidence of nonlinearities in the dose-response relationship. As an illustration, the bounding approach is applied to the case of chloroform exposure.

A comparison of Haber's rule at different ages using a physiologically based pharmacokinetic (PBPK) model for chloroform in rats

Haber's rule as commonly interpreted in inhalation toxicology, can be stated as exposure concentration times duration equals a constant biological effect, or C x t=k. In other words, identical products of concentration and duration lead to the same effect. The goals of this paper are to develop a biological and pharmacokinetic modeling approach for chloroform, and to evaluate Haber's rule for different ages by taking into account the physiological changes due to growth and aging in rats. Three-dimensional dose-response surfaces for liver toxicity were generated for each age group of interest: adolescent, adult, and senescent rats. The three-dimensional surfaces were then characterized with a generalized description of Haber's rule for each age group. The simulations suggest that adolescent rats need higher exposure levels in order to achieve similar levels of liver damage compared to adults or senescent rats, if the comparison is made using the same exposure length. In summary, a pharmacokinetic modeling approach with a biological framework including the chemical's mode of action, was used to relate concentration, exposure duration and effect. Major advantages of this approach include: the potential ability to extrapolate to humans, the inclusion of aging in the simulations, and the ability to summarize the results using a generalized form of Haber's rule.

Twenty-six-Week carcinogenicity study of chloroform in CB6F1 rasH2-transgenic mice

The carcinogenic potential of chloroform was evaluated in a short-term carcinogenicity testing system using CB6F1 rasH2-Tg (rasH2-Tg) mice. Chloroform was administered to rasH2-Tg males at doses of 28, 90, or 140 mg/kg and rasH2-Tg females at 24, 90, or 240 mg/kg by oral gavage for 26 weeks. Wild-type (non-Tg) male and female mice received doses of 140 mg/kg and 240 mg/kg, respectively. N-methyl-N-nitrosourea was administered to rasH2-Tg mice by single intraperitoneal injection (75 mg/kg) as a positive control. In both the rasH2-Tg and non-Tg mice, there was no significant increase in the incidence of neoplastic lesions by chloroform treatment. The incidence of hepatocellular foci in the rasH2- and non-Tg females receiving 240 mg/kg was increased. Forestomach tumors and malignant tumors occurred in most of the rasH2-mice in the positive control group. Swelling or vacuolation of hepatocytes, a toxic change induced by chloroform, occurred in both the rasH2-Tg and non-Tg mice. It is concluded that chloroform, a putative human noncarcinogen, did not show evidence of carcinogenic potential in the present study using rasH2-Tg mice. This study suggests that the rasH2-Tg mouse model may not be appropriate for detecting nongenotoxic carcinogens. However, the sensitivity of rasH2-Tg mice to nongenotoxic carcinogens should be assessed with consideration of the results from the other ILSI-HESI project studies.

Chloroform inhalation exposure conditions necessary to initiate liver toxicity in female B6C3F1 mice

Chloroform is a nongenotoxic-cytotoxic carcinogen in rodent liver and kidney, including the female B6C3F1 mouse liver. Because tumors are secondary to events associated with cytolethality and regenerative cell proliferation, these end points are valid surrogates for tumor formation in cancer risk assessments. The purpose of the experiments presented here was to more clearly define the combinations of atmospheric concentration and duration of exposure necessary to induce cytolethality and regenerative cell proliferation in the sensitive female B6C3F1 mouse liver. Female B6C3F1 mice were exposed to chloroform by inhalation for 7 consecutive days using atmospheres of 10, 30, or 90 ppm and selected exposure times of 2, 6, 12, or 18 h/day. Bromodeoxyuridine (BrdU) was given the last 3.5 days via an implanted osmotic pump to label cells in S-phase. Labeled hepatocytes were visualized immunohistochemically, and the labeling index (LI) was determined as the percentage of cells in S-phase. LI was a more sensitive indicator of cellular damage than histopathological examination and is the more conservative end point for use in risk assessments. Significant concentration and exposure time related increases in LI were observed at 30 and 90 ppm but not at any 10-ppm exposure. These data defined an empirical relationship for the combinations of airborne exposure concentration and duration needed to induce cytolethality. These results suggest that concentrations of about 10 ppm or below will not induce hepatotoxicity in these mice regardless of exposure duration. Thus, the rate of production of toxic metabolites and the subsequent rate of cellular damage produced by a continual exposure of approximately 10 ppm chloroform are less than the maximum rates at which hepatocytes can detoxify those metabolites and repair any induced cellular damage. A physiologically based pharmacokinetic (PBPK) dosimetry model was used to compare anticipated responses in mice and humans and predicted that chloroform concentrations of approximately an order of magnitude greater than 10 ppm would be required to induce human liver toxicity. Thus, no safety factor to account for species to species extrapolation should be required in formulating a chloroform inhalation cancer risk assessment based on the dose x time inhalation data presented here.

Classification of carcinogenic chemicals in the work area by the German MAK Commission: current examples for the new categories

The German Commission for the Investigation of Health Hazards of Chemical Compounds in the Work Area (MAK Commission) introduced an extended classification scheme in 1998. In addition to the traditional three categories still used to date, now called: Category 1 (human carcinogen); Category 2 (animal carcinogen); and Category 3 (suspected carcinogen), two new Categories (4 and 5) were added. Classification of substances into the new Categories 4 and 5 is based on the knowledge of mode of action and the potency of carcinogens. The essential feature of substances classified in the new Categories 4 and 5 is that exposure to these chemicals does not contribute significantly to the risk of cancer to man, provided that an appropriate exposure limit (MAK value) is observed. Chemicals known to act typically by non-genotoxic mechanisms are classified in Category 4. Genotoxic chemicals for which low carcinogenic potency can be assessed on the basis of dose-response relationships and toxicokinetics are classified in Category 5. Since the use of this scheme for 3 years, various chemicals have been classified in one of the new categories. However, in several cases data to sufficiently substantiate a MAK value are missing. Such substances are now classified in a subcategory of Category 3, called Category 3 A, which indicates that further data are required for final classification. Examples are given for classification of dichloromethane into Category 3 A, chloroform and sulfuric acid into Category 4 and ethanol into Category 5.

Optimization of an exogenous metabolic activation system for FETAX. II. Preliminary evaluation

The developmental toxicities of five test compounds including carbon tetrachloride, urethane, phenacetin, parathion, and chloroform, were evaluated using Frog Embryo Teratogenesis Assay--Xenopus (FETAX), with minor modification. Post-isolation mixtures of differently-induced rat liver microsomes (phenobarbital- (PB), beta-naphthoflavone- (beta-NF), and isoniazid- (INH)-induced preparations) were co-cultured directly with X. laevis embryos. Results from these studies suggest that the Aroclor 1254-induced MAS could effectively be replaced by a mixed lot of PB-, beta-NF-, and INH-induced rat liver microsomes. Each of the test materials were found to be developmentally toxic when bioactivated by the mixed MAS.

Effect of chloroform on dichloroacetic acid and trichloroacetic acid-induced hypomethylation and expression of the c-myc gene and on their promotion of liver and kidney tumors in mice

Chloroform, dichloroacetic acid (DCA) and trichloroacetic acid (TCA) are mouse liver carcinogens that are chlorine disinfection by-products found in drinking water. The effect of chloroform on DCA and TCA-induced hypomethylation and expression of the c-myc gene and on their promotion of liver and kidney tumors was determined. B6C3F1 mice were administered 0, 400, 800 and 1600 mg/l chloroform in drinking water and 500 mg/kg DCA or TCA-administered daily by gavage. DCA, TCA and to a lesser extent chloroform decreased the methylation and increased the mRNA expression of the c-myc gene. Co-administering chloroform prevented only DCA and not TCA-induced hypomethylation and increased mRNA expression of the gene. The effect of chloroform on tumor promotion by DCA and TCA was determined in female and male B6C3F1 mice initiated on day 15 of age with N-methyl-N-nitrosourea. Starting at 5 weeks of age, the mice received in their drinking water DCA (3.2 g/l) or TCA (4.0 g/l) with 0, 800 or 1600 mg/l chloroform until they were killed at 36 weeks. Liver tumors promoted by DCA and TCA were predominantly basophilic except for DCA-treated female mice that were eosinophilic. Only DCA promoted foci of altered hepatocytes and they were eosinophilic in both sexes. Chloroform prevented DCA, but not TCA promotion of liver foci and tumors. In male mice, TCA promoted kidney tumors while DCA promoted kidney tumors only when co-administered with chloroform. Hence, chloroform prevented the hypomethylation and increased mRNA expression of the c-myc gene and the promotion of liver tumors by DCA, while enhancing DCA-promotion of kidney tumors. Thus, the concurrent exposure to two carcinogens, chloroform and DCA resulted in less than additive activity in one organ and synergism in another organ.

Long-term effects on male reproduction of early exposure to common chemical contaminants in drinking water

We evaluated sequelae to early exposure of male rabbits to drinking water containing chemicals typical of ground water near hazardous waste sites. The mixture (p.p.m. at 1x) was 7.75 arsenic, 1.75 chromium, 9.25 lead, 12.5 benzene, 3.75 chloroform, 8.5 phenol and 9.5 trichloroethylene. Dutch-Belted does received mixture at 0x (deionized water; control), 1x or 3x as drinking water from day 20 pregnancy through weaning. Exposure of individual males (7-9/treatment) continued until 15 weeks (adolescence); then, all males received deionized water. At 57-61 weeks of age, ejaculatory capability and seminal, testicular, epididymal and endocrine characteristics were evaluated. At 10 opportunities with a female teaser, all seven control males ejaculated every time, but 12 of the 17 treated males failed to express interest, achieve erection and/or ejaculate on one to five occasions; four of the 12 accomplished ejaculation with a second male teaser. Total spermatozoa/ejaculate and daily sperm production were unaffected. However, treatment caused (P < 0.03) acrosomal dysgenesis and nuclear malformations. Baseline serum concentrations of LH were lower, but with borderline significance (P = 0.05). Testosterone secretion after exogenous human chorionic gonadotrophin (P < 0.04) was low. Thus, even at 45 weeks after last exposure to drinking water pollutants, mating desire/ability, sperm quality, and Leydig cell function were subnormal.

Correlation of a specific mitochondrial phospholipid-phosgene adduct with chloroform acute toxicity

The dose and time dependence of formation of a specific adduct between mitochondrial phospholipid and phosgene have been determined in the liver of Sprague-Dawley (SD) rats as well as in the liver and kidney of B6C3F1 mice after dosing with chloroform. Rats were induced with phenobarbital or non-induced. Determination of tissue glutathione (GSH) and of serum markers of hepatotoxicity and nephrotoxicity was also carried out. With dose-dependence experiments, a strong correlation between the formation of the specific phospholipid adduct, GSH depletion and organ toxicity could be evidenced in all the organs studied. With non-induced SD rats, no such effects could be induced up to a dose of 740 mg/kg. Time-course studies with B6C3F1 mice indicated that the specific adduct formation took place at very early times after chloroform dosing and was concurrent with GSH depletion. The adduct formed during even transient GSH depletion (residual level: 30% of control) and persisted after restoration of GSH levels. Following a chloroform dose at the hepatotoxicity threshold (150 mg/kg), the elimination of the adduct in the liver occurred within 24 h and correlated with the recovery of ALT, which was slightly increased (12 times) after treatment. Following a moderately nephrotoxic dose (60 mg/kg), the renal adduct persisted longer than 48 h, when a 100% increase in blood urea nitrogen and a 40% increase in serum creatinine indicated the onset of organ damage. The formation of the adduct in the liver mitochondria of B6C3F1 mice was associated with the decrease of phosphatidyl-ethanolamine (PE), in line with previous results in rat liver indicating that the adduct results from the reaction of phosgene with PE. The adduct levels implicated the reaction of phosgene with about 50% PE molecules in the liver mitochondrial membrane of phenobarbital-induced SD rats and of about 10% PE molecules of the inner mitochondrial membrane of the liver of B6C3F1 mice. The association of this adduct with the toxic effects of chloroform makes it a very good candidate as the primary critical alteration in the sequence of events leading to cell death caused by chloroform.

Chronic toxicity of chloroform to Japanese medaka fish

Japanese medaka (Oryzias latipes) were continually exposed in a flow-through diluter system for 9 months to measured chloroform concentrations of 0.017, 0.151, or 1.463 mg/L. Parameters evaluated were hepatocarcinogenicity, hepatocellular proliferation, hematology, and intrahepatic chloroform concentration. Histopathology was evaluated at 6 and 9 months. Chloroform was not hepatocarcinogenic to the medaka at the concentrations tested. Chronic toxicity was evidenced at these time points by statistically significant ([alpha] = 0.05) levels of gallbladder lesions and bile duct abnormalities in medaka treated with 1.463 mg/L chloroform. We assessed hepatocellular proliferation by exposing test fish to 5-bromo-2'-deoxyuridine in the aquarium water for 72 hr after 4 and 20 days of chloroform exposure; we then quantified area-labeling indices of the livers using computer-assisted image analysis. We observed no treatment-related increases in cellular proliferation. We analyzed cells in circulating blood in medaka after 6 months of chloroform exposure. Hematocrit, leukocrit, cell viability, and cell counts of treated fish were not significantly different from those of control fish. Using gas chromatography (GC), we evaluated intrahepatic concentrations of chloroform in fish after 9 months of exposure. Livers from the 0.151 and 1.463 mg/L chloroform-treated fish had detectable amounts of chloroform, but these levels were always lower than the aquaria concentrations of chloroform. Thus, it appeared that chloroform did not bioaccumulate in the liver. Unidentified presumptive metabolite peaks were found in the GC tracings of these fish livers.

The utility of PBPK in the safety assessment of chloroform and carbon tetrachloride

Occupational exposure limits (OELs) for individual substances are established on the basis of the available toxicological information at the time of their promulgation, expert interpretation of these data in light of industrial use, and the framework in which they sit. In the United Kingdom, the establishment of specific OELs includes the application of uncertainty factors to a defined starting point, usually the NOAEL from a suitable animal study. The magnitude of the uncertainty factors is generally determined through expert judgment including a knowledge of workplace conditions and management of exposure. PBPK modeling may help in this process by informing on issues relating to extrapolation between and within species. This study was therefore designed to consider how PBPK modeling could contribute to the establishment of OELs. PBPK models were developed for chloroform (mouse and human) and carbon tetrachloride (rat and human). These substances were chosen for examination because of the extent of their toxicological databases and availability of existing PBPK models. The models were exercised to predict the rate (chloroform) or extent (carbon tetrachloride) of metabolism of these substances, in both rodents and humans. Monte Carlo analysis was used to investigate the influence of variability within the human and animal model populations. The ratio of the rates/extent of metabolism predicted for humans compared to animals was compared to the uncertainty factors involved in setting the OES. Predictions obtained from the PBPK models indicated that average rat and mouse metabolism of carbon tetrachloride and chloroform, respectively, are much greater than that of the average human. Application of Monte Carlo analysis indicated that even those people who have the fastest rates or most extensive amounts of metabolism in the population are unlikely to generate the levels of metabolite of these substances necessary to produce overt toxicity in rodents. This study highlights the value that the use of PBPK modeling may add to help inform and improve toxicological aspects of a regulatory process.

Chlorinated methanes and liver injury: highlights of the past 50 years

The chlorinated methanes, particularly carbon tetrachloride and chloroform, are classic models of liver injury and have developed into important experimental hepatoxicants over the past 50 years. Hepatocellular steatosis and necrosis are features of the acute lesion. Mitochondria and the endoplasmic reticulum as target sites are discussed. The sympathetic nervous system, hepatic hemodynamic alterations, and role of free radicals and biotransformation are considered. With carbon tetrachloride, lipid peroxidation and covalent binding to hepatic constituents have been dominant themes over the years. Potentiation of chlorinated methane-induced liver injury by alcohols, aliphatic ketones, ketogenic compounds, and the pesticide chlordecone is discussed. A search for explanations for the potentiation phenomenon has led to the discovery of the role of tissue repair in the overall outcome of liver injury. Some final thoughts about future research are also presented.

Hepatoprotection by dimethyl sulfoxide. III. Role of inhibition of the bioactivation and covalent bonding of chloroform

Dimethyl sulfoxide (DMSO) has previously been shown to have the ability to attenuate chloroform (CHCl(3))-induced liver injury in the naive rat even when administered 24 h after the toxicant. These studies were undertaken to determine if the protective action by late administration of DMSO is due to an inhibition of the bioactivation of CHCl(3). This was done by comparing the cytochrome P450 inhibitors, diallyl sulfide (DAS), and aminobenzotriazole (ABT) to DMSO for their protective efficacy when administered 24 h after CHCl(3) exposure. In addition, (14)CHCl(3) was utilized to measure the effect of DMSO and ABT on the covalent binding of CHCl(3) in the liver following their late administration. Male Sprague-Dawley rats (300-350 g) received 0.75 ml/kg CHCl(3) po. Twenty-four hours later, they received ip injection of 2 ml/kg DMSO, 100 mg/kg DAS, or 30 mg/kg ABT. Plasma ALT activities and quantitation of liver injury by light microscopy at 48 h after CHCl(3) dosing indicated that all three treatments were equally effective at protecting the liver. A detailed study of the time course of injury development indicated that the protective action of DMSO was occurring within 10 h of its administration. Therefore, in the radiolabel studies, rats were killed 24-34 h after receiving 0.75 ml/kg CHCl(3) (30 microCi/kg (14)CHCl(3)) po. Treatment with ABT at 24 h after (14)CHCl(3) dosing decreased the covalent binding of (14)C to hepatic protein by 35% and reduced the amount of (14)C in the blood by 50% by 10 h after its administration. DMSO treatment did not significantly affect any of these parameters. The lack of effect by late administration of DMSO on the covalent binding of CHCl(3) would indicate that DMSO may offer protection by mechanisms other than inhibition of the bioactivation of CHCl(3). These studies also indicate that specific cytochrome P450 inhibitors may be of benefit in clinical situations to help treat the delayed onset hepatitis that can result following poisoning with an organohalogen, even if the antidotes are administered a number of hours after the initial exposure.