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Degradation of anthracene by laccase of Trametes versicolor in the presence of different mediator compounds.

Laccase of Trametes versicolor was generally able to oxidize anthracene in vitro. After 72 h incubation about 35% of the anthracene was transformed stoichiometrically to 9,10-anthraquinone. Transformation of anthracene increased rapidly in the presence of different mediators that readily generate stable radicals: 2,2'-azino-bis-(3-ethylbenzthiazoline-6-sulfonic acid) (ABTS) and 1-hydroxybenzotriazole. For the reaction, the presence of both the laccase and the mediator was necessary. In the presence of 0.005 mM 1-hydroxybenzotriazole this conversion had removed 47% of the anthracene after 72 h; 75% of the substrate was oxidized during this period when ABTS (1 mM) was used as mediator. In contrast to reactions without or with only low concentrations of a mediator, there was a discrepancy between the disappearance of anthracene and the formation of 9,10-anthraquinone in mediator-forced reactions. Coupling-products of mediators with anthracene degradation products were found. Anthracene disappeared nearly completely after incubation for 72 h with laccase in a 0.1 mM solution of 1-hydroxybenzotriazole and was transformed to 9,10-anthraquinone in about 80% yield; 90% of the substrate was transformed in the presence of ABTS (2.0 mM) resulting again in 80% quinone. Phenothiazine was not effective in this system.

Anthracenes↗

Uptake, depuration, and biotransformation of anthracene and benzo[a]pyrene in bluegill sunfish.

Bluegills (Lepomis macrochirus Raf.) were exposed to [14C]anthracene or [14C]benzo[a]pyrene (B[a]P) in water. Rates of uptake and biotransformation within the fish were followed by 14C counting and thin-layer and liquid chromatography. The initial uptake-rate coefficient for anthracene (KU = 36 hr-1) was found to be independent of exposure concentration. The presence of dissolved humics did not affect anthracene uptake but did reduce the B[a]P uptake rate significantly. Biotransformation of the anthracene was constant at 0.22 nmol/g/hr, with approximately 92% of the residue unmetabolized at 4 hr. Uptake of B[a]P was linear (KU = 49 hr-1), although biotransformation increased from 0.044 to 0.088 nmol/g/hr between 1 and 2 hr of exposure. Only 11% of the B[a]P 14C activity at 4 hr represented the parent compound. Although 6% of the anthracene was found in liver and gall bladder, 25% of the B[a]P was distributed in the two organs. Depuration rates were first order and yielded half-lives of 17 hr for anthracene and 67 hr for B[a]P. The estimated bioconcentration factors (BCF) for anthracene and B[a]P in whole fish (KU/KD) were 900 and 4900, respectively, for total 14C activity, but only 675 and 490 for parent material. These BCFs were considerably lower than those predicted from the octanol-water partition coefficients because of biotransformation.

Animals↗

Effects of surfactant and temperature on biotransformation kinetics of anthracene and pyrene.

The biotransformation and mineralization of a mixture of two polycyclic aromatic hydrocarbons (PAHs), anthracene and pyrene, which are known contaminants of soil and groundwater, by an enrichment culture in the presence or absence of 100 mg l(-1) Tergitol NP-10, a non-ionic surfactant, and at temperatures of 10 degrees C and 25 degrees C were investigated. The overall biotransformation of 2 mg l(-1) total PAHs with free cell suspensions in batch culture was greater than 97.2% at both examined temperatures. At 25 degrees C, the overall mineralization of anthracene was 48.8% and that of pyrene was 66.1%. However, the decrease of temperature to 10 degrees C had a negative effect on the mineralization of PAHs and reduced it to 18.5% and 61.5% for anthracene and pyrene, respectively. Using a higher PAHs concentration of 20 mg l(-1) at 25 degrees C, the overall biotransformation of anthracene was 80.7% and that of pyrene was 100%, where only 17.3% anthracene and 7.6% pyrene were mineralized to carbon dioxide and water. The addition of surfactant at 25 degrees C increased the overall mineralization of anthracene and pyrene to 33.0% and 27.6%, respectively. However, the addition of surfactant at 10 degrees C had a negative impact on the overall biotransformation of anthracene and pyrene, reducing them to 20.6% and 14.0%, respectively. These results have significant implications in the bioremediation of PAHs-contaminated sites.

Anthracenes↗

Carcinogenic activity of some benz(a)anthracene derivatives in newborn mice.

Equimolar doses of 7-methylbenz(a)anthracene and 3 of its derivatives were given to newborn male and female Swiss mice. All 4 substances tested increased the risk of tumour development compared with that seen in control mice given the vehicle, arachis oil, only.7-Methylbenz(a)anthracene itself was the most actively tumorigenic of the compounds studied, giving rise to subcutaneous sarcomata at the site of injection, and multiple lung tumours and liver tumours. 7-Bromomethyl-12-methylbenz(a)-anthracene was similarly active in the lung and liver but evoked fewer subcutaneous sarcomata. 7-Bromomethylbenz(a)anthracene was seemingly slightly less active than either 7-methylbenz(a)anthracene or 7-bromomethyl-12-methylbenz(a)anthracene. 4-Chloro-7-bromomethylbenz(a)anthracene exhibited only marginal activity in that it slightly increased the risk of liver tumour development in male mice.

Animals↗

Formation of bound residues during microbial degradation of [14C]anthracene in soil.

Carbon partitioning and residue formation during microbial degradation of polycyclic aromatic hydrocarbons (PAH) in soil and soil-compost mixtures were examined by using [14C]anthracenes labeled at different positions. In native soil 43.8% of [9-14C]anthracene was mineralized by the autochthonous microflora and 45.4% was transformed into bound residues within 176 days. Addition of compost increased the metabolism (67.2% of the anthracene was mineralized) and decreased the residue formation (20. 7% of the anthracene was transformed). Thus, the higher organic carbon content after compost was added did not increase the level of residue formation. [14C]anthracene labeled at position 1,2,3,4,4a,5a was metabolized more rapidly and resulted in formation of higher levels of residues (28.5%) by the soil-compost mixture than [14C]anthracene radiolabeled at position C-9 (20.7%). Two phases of residue formation were observed in the experiments. In the first phase the original compound was sequestered in the soil, as indicated by its limited extractability. In the second phase metabolites were incorporated into humic substances after microbial degradation of the PAH (biogenic residue formation). PAH metabolites undergo oxidative coupling to phenolic compounds to form nonhydrolyzable humic substance-like macromolecules. We found indications that monomeric educts are coupled by C-C- or either bonds. Hydrolyzable ester bonds or sorption of the parent compounds plays a minor role in residue formation. Moreover, experiments performed with 14CO2 revealed that residues may arise from CO2 in the soil in amounts typical for anthracene biodegradation. The extent of residue formation depends on the metabolic capacity of the soil microflora and the characteristics of the soil. The position of the 14C label is another important factor which controls mineralization and residue formation from metabolized compounds.

Anthracenes↗

Growth of rhodococcus S1 on anthracene.

Three slow-growing bacteria were isolated from a mixed culture enriched for growth on anthracene, using creosote-contaminated soil as the inoculum. Organisms were shown to use anthracene by the production of a clear zone around the colony after a mineral salts agar plate was sprayed with anthracene. All three bacteria were nonmotile, nonsporulating, gram-positive rods and stained acid-fast. Physiological and biochemical tests, GC content, and cell wall lipid patterns of whole cell methanolysates indicated that they belonged to the Nocardia-Mycobacterium-Rhodococcus group. On the basis of these characteristics and pyrolysis gas chromatography, they were assigned to the genus Rhodococcus. Growth of the isolates was slow on crystalline anthracene, giving a doubling time of 1.5-3 days, and they grew mainly on the crystal surface. When anthracene was supplied by precipitation from a solvent, doubling time was reduced to 1 day. All three isolates mineralized anthracene but not phenanthrene or naphthalene, nor could they grow on naphthalene, phenanthrene, fluorene, fluoranthene, acenaphthene, pyrene, chrysene, or naphthacene as sole carbon source. One isolate, Rhodococcus S1, was able to use 2-methylanthracene or 2-chloroanthracene as carbon source but not 1- or 9-substituted analogs. These results suggest that the initial enzyme attacking anthracene in these isolates has a narrow substrate specificity.

Anthracenes↗

Identification of toxic products of anthracene photomodification in simulated sunlight.

Currently, the evidence of a rapid photomodification of anthracene under sunlight resulting in enhanced toxicity exists; however, the chemical causes of toxicity are still unknown. The present study aimed at filling this gap by irradiation of an anthracene suspension with simulated sunlight and subsequent effect-directed fractionation and analysis of toxic products with respect to the inhibition of bacterial energy metabolism of Vibrio fischeri, reproduction of the green algae Scenedesmus vacuolatus, and genotoxicity in the umuC test. Algal toxicity of anthracene was hardly modified by irradiation prior to testing and distributed over all fractions with emphasis on the fractions containing anthracene-9,10-dione and a photometabolite suggested to be 10-hydroxyanthrone. Bacterial toxicity and genotoxicity in contrast emerged only when anthracene was irradiated. Anthracene-1,4-dione, a so-far-unknown trace photometabolite, was identified as a very potent toxicant dominating the toxicity of photomodified anthracene to V. fischeri. In genotoxic fractions, 1-hydroxyanthracene-9,10-dione and 1,4-dihydroxyanthracene-9,10-dione were identified and confirmed as genotoxicants. The results stress the potential of effect-directed analysis approaches in contrast to mere chemical analysis in studies aiming at toxicologically relevant photomodified substances.

Anthracenes↗

Cometabolic oxidation of phenanthrene to phenanthrene trans-9,10-dihydrodiol by Mycobacterium strain S1 growing on anthracene in the presence of phenanthrene.

Mycobacterium strain S1, originally described as Rhodococcus strain S1 by chemotaxonomic criteria, was isolated by growth on anthracene, and is unable to use any of nine other polycyclic aromatic compounds as carbon source. Metabolism of phenanthrene during growth on anthracene as sole carbon source results in the accumulation of traces of a dihydrodiol metabolite in the growth medium, which, by comparison with authentic standards, has been tentatively identified as phenanthrene trans-9,10-dihydrodiol. Anthracene metabolites were ruled out on the basis of comparisons with authentic anthracene dihydrodiols from Pseudomonas fluorescens D1 and chemically synthesized anthrols. The original source of phenanthrene for dihydrodiol production was phenanthrene present as a < 1% contaminant in the anthracene used as carbon source. However, addition of further phenanthrene to the anthracene growth medium increased the level of phenanthrene trans-9,10-dihydrodiol formed. Mycobacterium strain S1 also produced phenanthrene trans-9,10-dihydrodiol when grown in a glucose-salts medium in the presence of phenanthrene. This dihydrodiol is a dead-end metabolite, and neither it nor its parent hydrocarbon are able to support the growth of Mycobacterium strain S1. Studies with metyrapone and ancimidol, which did not inhibit growth on anthracene but did inhibit formation of phenanthrene trans-9,10-dihydrodiol, suggest it is likely the product of a cytochrome P450 monooxygenase-like activity.

Anthracenes↗

Phototoxicity of anthracene and pyrene to glochidia of the freshwater mussel Utterbackia imbecillis.

The acute toxicity of photoactivated anthracene and pyrene to the glochidial larvae of the paper pondshell (Utterbackia imbecillis) was characterized in the laboratory using two sets of experiments. Acute toxicity tests designed to determine the overall sensitivity of glochidia to anthracene and pyrene were conducted under simulated sunlight (ultraviolet [UV]-A = 70+/-0.5 microW/cm2 [mean +/- standard deviation]). The median lethal concentration (LC50) and median lethal dose (LD50) of anthracene at 24 h were 1.93 (95% CI, 0.87-3.02) microg/L and 1.94 (1.87-2.00) microg/g glochidia, respectively. The LC50 and LD50 for pyrene at 24 h were 2.63 (2.38-2.90) microg/L and 6.36 (5.82-6.94) microg/g glochidia, respectively. Acute toxicity tests designed to delineate the relationship between the rate of mortality and UV intensity were conducted under one of four different UV intensities (UV-A = 15, 31, 50, and 68 microW/cm2). Regression analyses revealed that time to death decreased as tissue residue concentrations and UV intensity increased for both compounds. Based on measured tissue residues, anthracene was 1.5-fold more potent than pyrene and 3-fold more potent than fluoranthene. The lower potency of fluoranthene is in agreement with previously developed structure-activity relationships; however, these relationships predict equal potency between anthracene and pyrene. These findings suggest that glochidia of freshwater mussels are sensitive to photoactivated anthracene and pyrene at environmentally relevant concentrations, that the time-dependent mortality of glochidia can be accurately predicted through evaluating the product of tissue residue and light intensity, and that species-dependent factors may alter the predicted relative potencies of anthracene and pyrene.

Animals↗

Biosynthesis of the potent carcinogen 7,12-dimethylbenz[a]anthracene.

Earlier studies from this laboratory of the metabolism of 7,12-dimethylbenz[a]anthracene (DMBA) and of benzo[a]pyrene as well as studies of mutagenic and carcinogenic activity of some of the metabolic products led to the concept that a necessary first step in carcinogenesis by most alkyl substituted polycyclic hydrocarbons is biotransformation to a meso-anthracenic hydroxyalkyl metabolite, whereas most hydrocarbons lacking alkyl substituents undergo a bio-alkylation substitution reaction in the mesoanthracenic position(s) or L-region as a necessary first step in carcinogenesis. According to this unified hypothesis, all strong polycyclic hydrocarbon carcinogens must either, themselves, bear a meso-anthracenic alkyl substituent or else undergo a bio-alkylation substitution reaction in vitro and in vivo. Here we report that the weak carcinogen benz[a]anthracene undergoes meso-anthracenic methylation by S-adenosyl-L-methionine (SAM), in the presence of a rat liver cytosol preparation, in vitro, to form DMBA and presumably the moderately active carcinogens 7-methylbenz[a]anthracene and 12-methylbenz[a]anthracene. These compounds are substrates for further L-region methylation to form the strong carcinogen, DMBA.

9,10-Dimethyl-1,2-benzanthracene↗

Inter- and intramolecular pi-stacking interactions in cis-bis[1-(9-anthracene)]phosphirane complexes of platinum(II).

The bis[1-(9-anthracene)phosphirane]dithiolatoplatinum(II) complexes, Pt[1-(9-anthracene)phosphirane](2)(dithiolate), where dithiolate = 1,1-dimethoxycarbonyl-ethylene-2,2-dithiolate (dmdt) (2), 1,1-diethoxycarbonyl-ethylene-2,2-dithiolate (dedt) (3), 1-ethoxycarbonyl-1-cyano-ethylene-2, 2-dithiolate (ecdt) (4), and 1,1-dicyano-ethylene-2,2-dithiolate (dcdt) (5), were prepared from cis-dichlorobis[1-(9-anthracene)phosphirane]platinum(II) (1). Complexes 3 and 5 were characterized by X-ray crystallography and were found to have vastly different crystal and molecular structures. The crystal and molecular structure of 3 is dominated by intramolecular pi-stacking between the anthracene rings of the cis-bis(anthracene)phosphiranes with a ring...ring separation of 3.48(6) A. The molecular structure of 5 does not exhibit an intramolecular interaction between the anthracene rings. Instead, the crystal structure of 5shows significant intermolecular pi-stacking between the anthracene rings of the phosphirane ligands of adjacent molecules packed in the crystal lattice. The intermolecular stacking interaction results in a ring...ring separation of 3.33(4) A. Complexes 2-5 were found to emit at 530 nm at low temperatures in the solid state. Complex 5 emits strongly in fluid THF or benzene solution at 430 nm.

Journal Article↗

Scanning tunneling microscopy of prochiral anthracene derivatives on graphite: chain length effects on monolayer morphology.

The morphology of monolayers formed upon adsorption of prochiral 1,5-substituted anthracene derivatives on highly oriented pyrolytic graphite is investigated using scanning tunneling microscopy at the liquid-solid interface. The adsorption orientation of these prochiral anthracene derivatives positions one of their enantiotopic faces in contact with the graphite. The molecules adsorb in rows with contact between adjacent anthracenes. The anthracene side chains extend perpendicular to the direction of the row repeat. All molecules within a single row adsorb via the same enantiotopic face. Anthracenes with side chains containing an even number of non-hydrogenic atoms (C, S) form monolayers in which molecules in adjacent rows adsorb via opposite enantiotopic faces. Anthracenes with side chains that contain an odd number of non-hydrogenic atoms form two-dimensional chiral domains in which all rows contain molecules adsorbed via the same enantiotopic face. This chain length effect on monolayer morphology represents a generalized example of structural effects previously observed in alkanoic acid monolayers formed on HOPG. The variation of the STM current with position in the vicinity of the anthracenes indicates that the highest occupied molecular orbital is the predominant mediator of tunneling for the aromatic group.

Journal Article↗

The effect of the bay-region 12-methyl group on the stereoselective metabolism at the K-region of 7,12-dimethylbenz[a]anthracene by rat liver microsomes.

The enantiomers of a trans-5,6-dihydrodiol formed in the metabolism of 7,12-dimethylbenz[a]anthracene by rat liver microsomes (microsomal fractions) were resolved by chiral stationary-phase high-performance liquid chromatography. The major 7,12-dimethylbenz[a]anthracene trans-5,6-dihydrodiol enantiomer and its hydrogenation product 5,6,8,9,10,11-hexahydro-trans-5,6-diol were found to have 5S,6S absolute configurations by the exciton chirality c.d. method. The R,R/S,S enantiomer ratios of 7,12-dimethylbenz[a]anthracene trans-5,6-dihydrodiol formed in the metabolism of 7,12-dimethylbenz[a]anthracene by liver microsomes from untreated, 3-methylcholanthrene-treated and phenobarbital-treated male Sprague-Dawley rats were found to be 11:89, 6:94, and 5:95 respectively. These findings and those reported previously on the metabolic formations of trans-5,6-dihydrodiols from 7-methylbenz[a]anthracene and 12-methylbenz[a]anthracene suggest that the 12-methyl group in 7,12-dimethylbenz[a]anthracene plays an important role in determining the stereoselective metabolism at the K-region 5,6-double bond. Furthermore, the finding that formation of 5S,6S-dihydrodiol as the predominant enantiomer was not significantly affected by the isoenzymic composition of cytochrome P-450 present in microsomes prepared from the livers of the rats pretreated with the different inducing agents indicates that the stereoselectivity depends on the substrate metabolized rather than on the precise nature of the metabolizing-enzyme system.

9,10-Dimethyl-1,2-benzanthracene↗

Molecular mechanism of 7,12-dimethylbenz[a]anthracene-induced immunosuppression: evidence for action via the interleukin-2 pathway.

Previous studies in this laboratory have demonstrated that exposure of mice to the carcinogenic polycyclic aromatic hydrocarbon 7,12-dimethylbenz[a]anthracene results in suppression of both humoral and cell-mediated immunity. This suppression is unaccompanied by any significant alteration in splenic lymphocyte subpopulation composition, suggesting that the immune deficit was due to a modulation of lymphocyte function. Additional studies implicated the T helper lymphocyte as the probable target for 7,12-dimethylbenz[a]anthracene-induced immunosuppression, apparently through an inhibition of interleukin 2 production. The purpose of the present study was to examine the mechanism of 7,12-dimethylbenz[a]anthracene-induced T lymphocyte dysfunction at the molecular level and to determine the consequences of 7,12-dimethylbenz[a]anthracene exposure on the interleukin 2 pathway. In vitro exposure of Con A-activated splenocytes to 7,12-dimethylbenz[a]anthracene resulted in suppression of the mitogenic response, suppressed interleukin 2 production, and reduced the expression of the high affinity receptor for interleukin 2. In contrast, expression of the low affinity interleukin 2 receptor was not affected. In addition, interleukin 2-dependent lymphoblasts and long term cultured splenocytes exhibited a dose-dependent decrease in proliferation following in vitro exposure to 7,12-dimethylbenz[a]anthracene. These results suggest that 7,12-dimethylbenz[a]anthracene-induced immunosuppression may be mediated, at least in part, through the interleukin 2/interleukin 2 receptor pathway.

9,10-Dimethyl-1,2-benzanthracene↗

Potential carcinogenicity of aza-aromatic hydrocarbons: azabenz(a)anthracenes.

The potential carcinogenicity of 3 azabenz(a)anthracenes was determined in vitro. The 3 compounds tested were 1-, 2-, and 9-azabenz(a)anthracene. The initial assay was chemical carcinogen-induced enhancement of anchorage-independent survival of Rauscher leukemia virus-infected Fischer rat embryo cells, 2FR(4)50 (2FR4). Cells treated with 2- and 9-azabenz(a)anthracene showed dose-dependent increased survival. After continued subculturing, the surviving cells from 2- and 9-azabenz(a)anthracene-treated cultures displayed morphological transformation and ability to grow in semi-solid medium. Mock-treated controls and I-azabenz(a)anthracene-treated cultures did not show either of these properties. These data suggest that certain azabenz(a)anthracenes are potential carcinogens.

4-Nitroquinoline-1-oxide↗

Fluorescence and photoelectron studies of the intercalative binding of benz(a)anthracene metabolite models to DNA.

DNA binding of nonreactive metabolite models derived from benz(a)anthracene was studied. The molecules investigated include 1,2,3,4-tetrahydrobenz(a)anthracene (1), 5,6-dihydrobenz(a)anthracene (2), and 8,9,10,11-tetrahydrobenz(a)anthracene (3), as well as anthracene and phenanthrene. Measurements of the effects of DNA binding upon fluorescence intensities and fluorescence lifetimes indicate that molecules 1 and 3 (KA = 1.5 - 2.5 x 10(3) M-1) bind more strongly to native DNA than does molecule 2 (KA congruent to 0.5 x 10(3) M-1). Furthermore, molecules 1 and 3 bind to DNA much more effectively than do the two less sterically hindered pi electron metabolite models, anthracene and phenanthrene. Photoelectron data suggests that the enhanced binding of molecules 1 and 3 is due to increases in polarizability. Experiments carried out with denatured DNA indicate that the binding of molecule 1 entails the greatest intercalation.

Benz(a)Anthracenes↗

Differential gene expression in anthracene-exposed mummichogs (Fundulus heteroclitus).

The polycyclic aromatic hydrocarbon (PAH) anthracene is present in many estuarine systems at concentrations believed to cause sublethal adverse effects, although its exact mode of toxicity remains unclear. Knowledge of the induction or suppression of specific genes as a result of exposure may be useful in explaining these effects. We have generated a fingerprint of anthracene exposure using the mummichog (Fundulus heteroclitus), a non-migratory estuarine fish species. The fish were exposed in 7-day static renewal tests to environmentally relevant concentrations of 0, 27, 50, and 80 microg/l of anthracene. Total RNA was extracted from the livers and differential display reverse transcription polymerase chain reaction (DD RT-PCR) was used to recover 26 differentially expressed cDNA fragments. These cDNAs were isolated, sequenced, and compared to sequences of known genes in order to identify possible physiological consequences of exposure to anthracene. We then constructed macroarrays using these fragments and probed them with RNA from both anthracene-exposed fish and fish from a known PAH-impacted site. Three genes appear to be good indicators of exposure to anthracene in the range of concentrations tested, which included CYP2N2 and two expressed sequence tags (ESTs) termed 15C1 and 18C2. The expression of nine genes was altered in fish collected from a site with multiple PAHs. Band 15C1 and CYP2N2 again showed statistically significant upregulation in the field-caught fish, while a trypsin precursor and fatty acid-binding protein (FABP) all showed similar trends in induction as the laboratory-exposed fish. Further insight into the mechanism of toxicity of contaminants will be gained by the ability to identify and use differentially expressed genes as markers of exposure and effects.

Analysis of Variance↗

Breakdown products on metabolic pathway of degradation of benz[a]anthracene by a ligninolytic fungus.

Cultures of the ligninolytic fungus Irpex lacteus incubated in a nutrient liquid medium degraded more than 70% of the initially applied benz[a]anthracene within 14 days. At the first step of metabolization, benz[a]anthracene was transformed via a typical pathway of ligninolytic fungi to benz[a]anthracene-7,12-dione (BaAQ). The product was further transformed by at least two ways, whereas one is complied with the anthracene metabolic pathway of I. lacteus. Benz[a]anthracene-7,12-dione was degraded to 1,2-naphthalenedicarboxylic acid and phthalic acid that was followed with production of 2-hydroxymethyl benzoic acid or monomethyl and dimethylesters of phthalic acid. Another degradation product of BaAQ was identified as 1-tetralone. Its transformation via 1,4-naphthalenedione, 1,4-naphthalenediol and 1,2,3,4-tetrahydro-1-hydroxynaphthalene resulted again in phthalic acid. None of the intermediates were identified as dead-end metabolites. Metabolites produced by ring cleavage of benz[a]anthracene using the ligninolytic fungus are firstly presented in this work.

Basidiomycota↗