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At least 37 records · Page 2Linked to original sources
PubMed1984

Mechanism of chloroform nephrotoxicity. IV. Phenobarbital potentiation of in vitro chloroform metabolism and toxicity in rabbit kidneys.

Metabolism of chloroform (CHCl3) by a cytochrome P-450-dependent process to a reactive metabolite may be required to elicit hepatic and renal toxicities. Specific inducers or inhibitors of cytochrome P-450 have been employed frequently as tools to demonstrate this relationship between metabolism and toxicity in the liver. The experiments reported herein were designed to identify the relationship between metabolism and toxicity of CHCl3 in the kidney of rabbits, a species in which renal cytochrome P-450 is induced by phenobarbital. Pretreatment with phenobarbital enhanced the toxic response of renal cortical slices to CHCl3 in vitro as indicated by decreased p-aminohippurate and tetraethylammonium accumulation. Phenobarbital pretreatment also potentiated in vitro 14CHCl3 metabolism to 14CO2 and covalently bound radioactivity in rabbit renal cortical slices and microsomes. Addition of L-cysteine significantly reduced covalent binding in renal microsomes from both phenobarbital-treated and control rabbits and was associated with the formation of the radioactive phosgene-cysteine conjugate 2-oxothiazolidine-4-carboxylic acid (OTZ). Formation of OTZ was enhanced in renal microsomes from phenobarbital-pretreated rabbits. Thus, this in vitro model supports the hypothesis that the kidney metabolizes CHCl3 to the nephrotoxic metabolite, phosgene.

Animals↗
PubMedDate not supplied

Strain and sex differences in chloroform-induced nephrotoxicity. Different rates of metabolism of chloroform to phosgene by the mouse kidney.

It has been known for many years that there are species, strain, and sex differences in the incidence and severity of the nephrotoxicity caused by chloroform. However, the molecular basis for these differences has not been clearly understood. In this investigation, we have found that sensitivity to CHCl3 correlates with the capacity of the kidney to metabolize CHCl3 to the toxic metabolite phosgene (COCl2). For example, kidney homogenates of sensitive male DBA/2J mice metabolized CHCl3 to COCl2 more rapidly than did the less sensitive C57BL/6J mice. Similarly, kidney homogenates from male mice, which are sensitive to CHCl3-induced nephrotoxicity, metabolized CHCl3 to COCl2 at nearly an order of magnitude more rapidly than did those from female mice. Treatment of female mice with testosterone, however, reversed this trend. Cytochrome P-450 in the microsomal and mitochondrial fraction of the kidney appeared to catalyze the metabolism of CHCl3 to COCl2.

Animals↗
PubMed1998

Chloroform-induced cytolethality in freshly isolated male B6C3F1 mouse and F-344 rat hepatocytes.

Chloroform is carcinogenic in rodents but is not mutagenic or DNA reactive. Chloroform-induced hepatocarcinogenesis in rodents is believed to be secondary to events associated with cytotoxicity and cell proliferation. Understanding the mechanisms of chloroform toxicity may provide insights into the mechanisms of carcinogenicity. The goal of these studies was to characterize the cytotoxicity of chloroform in male B6C3F1 mouse and F-344 rat hepatocytes in vitro. We used an in vitro suspension-culture system that reproduced the exposure of the liver to chloroform and the expression of toxicity in vivo. Simulations of a physiologically based dosimetry model for chloroform indicated that the livers of mice and rats were exposed to chloroform concentrations up to 5 mM for 3 h after hepatotoxic doses of chloroform. Freshly isolated male mouse and rat hepatocytes were exposed to chloroform in sealed flasks and then cultured for 24 h as monolayers. Following a 2- or 3-h exposure in suspension, chloroform induced concentration-dependent cytotoxicity (lactate dehydrogenase release) in culture at concentrations higher than 1 mM. Cytolethality was not increased under reduced oxygen tension, indicating that reductive metabolism does not contribute to chloroform-induced toxicity. A threshold of 1 mM chloroform was also found for glutathione (GSH) depletion, with a 50% depletion at 3.8 mM after 2 h. Addition of dithiothreitol, a reducing agent, did not prevent chloroform-induced toxicity, indicating that oxidation of sulfhydryl groups is not critical for toxicity. The lack of protein sulfhydryl group depletion is consistent with this conclusion. Cotreatment with the cytochrome P450 inhibitor 1-phenylimidazole prevented both cytolethality and GSH depletion, indicating that metabolism is necessary for chloroform-induced toxicity. Both species exhibited similar sensitivity toward chloroform toxicity, indicating that toxicity is not sufficient to explain different susceptibility in heptocarcinogenicity. As chloroform metabolism is saturated in the micromolar range, our results indicate that both metabolism and exposure of the liver cells to high concentrations of chloroform are required for toxicity.

Animals↗
PubMed2000

Chloroform-induced conformational changes in the bound pigmentin bilirubin-albumin complexes.

Chloroform-induced conformational changes of bilirubin (BR) bound to different serum albumins were studied by circular dichroism (CD) and fluorescence spectroscopy. Addition of a small amount of chloroform ( approximately 20 mM) to a solution containing 20 microM albumin and 15 microM BR changed the sign order and magnitude of the characteristic CD spectra of all BR-albumin complexes except BR-PSA complex which showed abnormal behavior. Monosignate negative CD Cotton effects (CDCEs) of BR complexed with SSA, GSA and BuSA were transformed into bisignate CDCEs in presence of chloroform akin to those exhibited by chloroform free solution of BR-HSA complex, indicating that the pigment acquired right handed plus (P) chirality when chloroform was added to these complexes. Bisignate CD spectra of BR complexed with HSA and BSA showed complete inversion upon addition of chloroform corroborating earlier findings. On the other hand, changes observed with BR-RSA complex were slightly different showing an additional CD band of weak intensity centered around 390 nm though inversion of CDCEs was similar to that of BR-HSA complex. Monosignate CD spectra of BR-PSA complex also showed three CD bands occurring at 409, 470 and 514 nm after chloroform addition. These results indicated significant but different effects of chloroform on the conformation of bound BR in BR-albumin complexes which can be ascribed to the changes in the exciton chirality of bilirubin probably due to altered hydrophobic microenvironment induced by the binding of chloroform at or near the ligand binding site. Chloroform severely quenched the intrinsic tryptophan fluorescence of the protein and shifted the emission maxima towards blue region in all the albumins except PSA. However, quantitative differences in both quenching and blue shift were noted in different serum albumins. This suggests that chloroform probably binds in the close vicinity of tryptophan residue(s) located in subdomain(s) IIA or IB and II both. The fluorescence of BR-albumin complexes was also found to be sensitive to the presence of a small amount of chloroform. But the changes observed in the fluorescence of the bound pigment in presence of chloroform were less marked as compared to the changes in the intrinsic fluorescence of protein per se. Taken together, these results suggest that there is at least one conserved site for chloroform binding in all these albumins which is at or near the BR binding site.

Bilirubin↗
PubMed1997

[History of chloroform anesthesia].

The first narcosis with chloroform was performed by James Young Simpson on himself on November 4, 1847. The chemical substance had been first produced in 1831 almost simultaneously in the USA by Samuel Guthrie and in France by Eugène Soubeiran. Knowledge of the narcotic effect of chloroform spread rapidly, but very soon reports of sudden deaths mounted. The first fatality was a 15-year-old girl called Hannah Greener, who died on January 28, 1848. The opponents and supporters of chloroform were mainly at odds with the question of whether the complications were solely due to respiratory disturbance or whether chloroform had a specific effect on the heart. Between 1864 and 1910 numerous commissions in UK studied chloroform, but failed to come to any clear conclusions. It was only in 1911 that Levy proved in experiments with animals that chloroform can cause cardiac fibrillation. The reservations about chloroform could not halt its soaring popularity. Between about 1865 and 1920, chloroform was used in 80 to 95% of all narcoses performed in UK and German-speaking countries. In America, however, there was less enthusiasm for chloroform narcosis. In Germany the first comprehensive surveys of the fatality rate during anaesthesia were made by Gurlt between 1890 and 1897. In 1934, Killian gathered all the statistics compiled until then and found that the chances of suffering fatal complications under ether were between 1: 14,000 and 1: 28,000, whereas under chloroform the chances were between 1: 3,000 and 1: 6,000. The rise of gas anaesthesia using nitrous oxide, improved equipment for administering anaesthetics and the discovery of hexobarbital in 1932 led to the gradual decline of chloroform narcosis. In 1947, Ralph Waters attempted to reactivate chloroform, but failed. Possibly as a result of these efforts, however, chloroform played a role in American publications longer than elsewhere. The story of the clinical use of chloroform ended in 1976 with the second edition of V. J. Collins' textbook.

Adolescent↗
PubMed1994

Induced cytotoxicity and cell proliferation in the hepatocarcinogenicity of chloroform in female B6C3F1 mice: comparison of administration by gavage in corn oil vs ad libitum in drinking water.

Chloroform increases the incidence of liver tumors in B6C3F1 mice when administered in by gavage in corn oil, but not when given in the drinking water at similar daily doses. Since cytotoxicity and regenerative cell proliferation have been implicated in the tumorigenic process for this nongenotoxic agent, these effects of chloroform in corn oil and drinking water were evaluated under conditions similar to the two bioassays. Female B6C3F1 mice were administered oral doses of 0, 3, 10, 34, 90, 238, or 477 mg/kg chloroform dissolved in corn oil 5 days/week for periods of 4 days or 3 weeks, or were continually exposed to chloroform in the drinking water at concentrations of 0, 60, 200, 400, 900, or 1800 ppm for 4 days or 3 weeks, at which time they were necropsied. 5-Bromo-2'-deoxyuridine (BrdU) was delivered via osmotic pumps implanted 3.5 days prior to necropsy. Cell proliferation was evaluated as the percentage of hepatocytes that entered S-phase over 3.5 days (labeling index, LI), measured by immunohistochemical detection of BrdU incorporated into the DNA. Dose-dependent changes included centrilobular necrosis and markedly elevated LI in mice given 238 or 477 mg/kg chloroform in corn oil (the average daily doses that produced tumors in the cancer bioassay). The no-observed-effect level for histopathological changes was 10 mg/kg/day and for induced cell proliferation was 34 mg/kg/day for chloroform given in corn oil. Chloroform given in the drinking water did not increase the hepatic LI after either 4 days or 3 weeks in any of the dose groups, nor were any microscopic alterations observed in the livers, even though the cumulative daily amount of chloroform ingested in the 1800-ppm exposure group was 329 mg/kg/day. The sustained increase in LI in the livers of mice administered hepatocarcinogenic doses of chloroform in corn oil, but not for chloroform in drinking water, is evidence that chloroform-induced mouse liver cancer is secondary to events associated with induced cytolethality and cell proliferation. The triggering of these effects appears to be dependent on both the rate and duration of chloroform delivery to the target tissues. Thus, the most straightforward risk assessment for chloroform for this tissue would assign no increased cancer risk for dosing regimens that do not induce cytolethality and cell proliferation.

Administration, Oral↗
PubMed1985

Chloroform-induced alteration of glutathione S-transferase activity.

The effect of chloroform treatment on the hepatic glutathione S-transferases was studied in phenobarbital-treated rats. The apparent isozymic composition of glutathione S-transferases in hepatic cytosol was changed after chloroform treatment. Glutathione S-transferases AA, A, B, C, and D + E were observed in hepatic cytosol from untreated rats; in contrast, the catalytic activity associated with basic glutathione S-transferases, such as AA, A, B, and C, decreased with time after chloroform treatment. Glutathione S-transferase B was not detectable 2 hr after chloroform treatment, and glutathione S-transferases AA and C were scarcely detectable after 5 hr. Twenty-four hours after chloroform treatment, glutathione S-transferases A and C were clearly detectable as was D + E and a small amount of B. Hepatic cytosolic glutathione S-transferase activity was decreased by chloroform treatment, and reached a minimum at 5 hr after treatment. Corresponding to the decrease of hepatic cytosol glutathione S-transferase activity, serum glutathione S-transferase activity was elevated maximally 5 hr after chloroform treatment and returned to almost normal by 24 hr. Treatment of rats with SKF 525-A or cysteine inhibited the chloroform-induced elevation of serum glutathione S-transferase activity. The chromatographic properties of the glutathione S-transferases present in serum were similar to glutathione S-transferase D + E. Furthermore, after incubation of partially purified cytosolic glutathione S-transferases with chloroform in the presence of hepatic microsomes and NADPH, only transferase D + E was detected. The addition of bilirubin to partially purified cytosolic glutathione S-transferase decreased the basic character of glutathione S-transferases B and C. In conclusion, chloroform caused a release of hepatic cytosolic glutathione S-transferases into serum. Both the active metabolite of chloroform, which was produced by the microsomal cytochrome P-450 system, and bilirubin, which was increased by chloroform treatment, played roles in altering the properties of the glutathione S-transferases.

Animals↗
PubMed1995

Chloroform degradation in methanogenic methanol enrichment cultures and by Methanosarcina barkeri 227.

The effects of methanol addition and consumption on chloroform degradation rate and product distribution in methanogenic methanol enrichment cultures and in cultures of Methanosarcina barkeri 227 were investigated. Degradation of chloroform with initial concentrations up to 27.3 microM in enrichment cultures and 4.8 microM in pure cultures was stimulated by the addition of methanol. However, methanol consumption was inhibited by as little as 2.5 microM chloroform in enrichment cultures and 0.8 microM chloroform in pure cultures, suggesting that the presence of methanol, not its exact concentration or consumption rate, was the most significant variable affecting chloroform degradation rate. Methanol addition also significantly increased the number of moles of dichloromethane produced per mole of chloroform consumed. In enrichment cultures, the number of moles of dichloromethane produced per mole of chloroform consumed ranged from 0.7 (methanol consumption essentially uninhibited) to 0.35 (methanol consumption significantly inhibited) to less than 0.2 (methanol not added to the culture). In pure cultures, the number of moles of dichloromethane produced per mole of chloroform consumed was 0.47 when methanol was added and 0.24 when no methanol was added. Studies with [14C]chloroform in both enrichment and pure cultures confirmed that methanol metabolism stimulated dichloromethane production compared with CO2 production. The results indicate that while the addition of methanol significantly stimulated chloroform degradation in both methanogenic methanol enrichment cultures and cultures of M. barkeri 227, the prospects for use of methanol as a growth substrate for anaerobic chloroform-degrading systems may be limited unless the increased production of undesirable chloroform degradation products and the inhibition of methanol consumption can be mitigated.

Biodegradation, Environmental↗
PubMed2003

Comparison of different chloroformates for the derivatisation of seleno amino acids for gas chromatographic analysis.

Three chloroformate reagents, ethyl chloroformate (ECF), methyl chloroformate (MCF) and menthyl chloroformate (MenCF), have been used for the derivatisation of seleno amino acids and their performance was compared. Chromatographic parameters and the inertness of the different instrumental configurations used (gas chromatography-atomic emission detection (GC-AED), and GC-MS) were shown to have a significant influence on the detection of various seleno amino acids (selenomethione, selenoethione and selenocysteine) and some sulphur-containing amino acids (methionine, cysteine, cystine and methylcysteine) which were included in the experiments for comparison. Methyl chloroformate was the preferred derivatisation reagent, since it generally performed best in terms of derivatisation yield and reproducibility and also showed less significant conditioning effects than ethyl chloroformate. Methyl and ethyl chloroformate derivatives of selenomethionine, selenoethionine, cysteine and methionine were detectable, while the detection of the menthyl chloroformate derivatives of selenocystine and cystine was not reproducible. Overall efficiencies for the determination of selenomethionine and selenoethionine from aqueous extracts ranged from 40 to 100% for methyl chloroformate, over 30-75% for ethyl chloroformate to 15-70% for menthyl chloroformate for different series measured over a period of months. The relative standard deviation of the method for the methyl and menthyl chloroformate derivatisation ranged from 7 to 13% without internal standard and was improved to 2% for the determination of selenomethionine using selenoethionine as internal standard. This indicates that, despite the limited reproducibility of the method, its repeatability is good enough to allow accurate determination of seleno amino acids, which was also demonstrated by the analysis of selenium supplementation tablets for human diet that contained selenomethionine.

Amino Acids↗
PubMed1997

Chloroform mode of action: implications for cancer risk assessment.

Risk assessment methodology, particularly pertaining to potential human carcinogenic risks from exposures to environmental chemicals, is undergoing intense scrutiny from scientists, regulators, and legislators. The current practice of estimating human cancer risk is based almost exclusively on extrapolating the results of chronic, high-dose studies in rodents to estimate potential risk in humans. However, many scientists are questioning whether the logic used in this current risk assessment methodology is the best way to safeguard public health. A major tool of human cancer risk assessment is the linearized multistage (LMS) model. The LMS model has been identified as an aspect of risk assessment that could be improved. One way to facilitate this improvement is by developing a way to incorporate a carefully derived, more biologically relevant mechanism of action data on carcinogenesis. Recent data on chloroform indicate that the dose-response relationship for chloroform-induced tumors in rats and mice is nonlinear, based upon events secondary to cell necrosis and subsequent regeneration as the likely mode of action for the carcinogenic effects of chloroform. In light of these data, there is a sound scientific basis for removing some of the uncertainty that accompanies current cancer risk assessments of chloroform. The following points summarize the critical data: (1) a substantial body of data demonstrates a lack of direct in vivo or in vitro genotoxicity of chloroform; (2) chloroform induces liver and kidney tumors in long-term rodent cancer bioassays only at doses that induce frank toxicity at these target sites; (3) the chloroform doses required to produce tumors in susceptible species exceed the MTD, often by a considerable margin; (4) cytotoxicity and compensatory cell proliferation are associated with the chloroform doses required to induce liver or kidney tumors in susceptible rodent species; (5) there are no instances of chloroform-induced tumors that are not preceded by this pattern of dose-dependent toxic responses; (6) it is biologically plausible that cytolethality leads to chronically stimulated cell proliferation and related events such as inflammation and growth stimulation which act to initiate and promote the carcinogenic process; and (7) the consistently linked cellular events of cytolethality and subsequent cell proliferation, for which doses of no adverse effect have been clearly shown to exist, are one of the biological prerequisites for chloroform-induced tumors in animals. Based on these data, it is inappropriate to extrapolate cancer risk from high doses that produce necrosis and regenerative cell proliferation to low doses that do not with a model that presumes genotoxicity and a linear dose-response relationship. The weight of the scientific evidence concerning chloroform-induced tumors in rodents is consistent with and supports a cancer risk assessment methodology based on mode of action as the basis for establishing regulatory standards for this compound.

Administration, Inhalation↗