Utilization of chlorobenzoates by microbial populations in sewage.

Microorganisms in sewage decomposed 3.4-dichlorobenzoate and m-, p-, and o-chlorobenzoates. As the substrate disappeared, populations capable of growing on these compounds proliferated. Neither 2,4-dichlorobenzoate nor 2,3,6-trichlorobenzoate was destroyed by the sewage microflora. The addition of glucose or benzoate and m-chlorobenzoate to the sewage did not promote degradation of 2,4-di- or 2,3,6-trichlorobenzoates. The populations responsible for the biodegradation of the chlorinated compounds were initially less than 100 cells/ml. During the metabolism of m-chlorobenzoate, 5-chlorosalicylate and 4-chlorocatechol were formed.     

Co-metabolism of di- and trichlorobenzoates in a 2-chlorobenzoate-degrading bacterial culture: Effect of the position and number of halo-substituents

The degradative properties towards chlorobenzoates by a 2-chlorobenzoate-degrading mixed culture (2MC) were investigated. Although 2MC did not grow on 2,3,5-; 2,3,6- and 2,4,6-trichlorobenzoates, it was able to completely oxidise 2,3,5-trichlorobenzoate and 2,5-dichlorobenzoate. This was degraded through the intermediate formation of 4-chlorocatechol and 3-cis,cis-chloromuconate, suggesting a dioxygenation in 1,2 position. 4-Chlorobenzoate; 3,4- and 2,6-dichlorobenzoate; 2,4,6- and 2,3,6-trichlorobenzoate did not undergo any co-metabolic transformation, the only 2,4-dichlorobenzoate was scarcely transformed into a dichlorinated phenol as end-product. 2MC was constituted of three prominent species: Stenotrophomonas maltophilia, Cupriavidus necator and Flavobacterium sp. Ring-hydroxylating dioxygenase genes (BenA) were retrieved in S. maltophilia and C. necator, indicating the presence of a “modified ortho pathway” in the culture. On the basis of its degradative properties, 2MC could be a good candidate for use in the removal of ortho- and/or meta-chlorobenzoates that are the major end-products of PCB co-metabolism.     

Metabolism of and inhibition by chlorobenzoates in Pseudomonas putida P111.

Pseudomonas putida P111 was isolated by enrichment culture on 2,5-dichlorobenzoate and was also able to grow on 2-chloro-, 3-chloro-, 4-chloro-, 2,3-dichloro-, 2,4-dichloro-, and 2,3,5-trichlorobenzoates. However, 3,5-dichlorobenzoate completely inhibited growth of P111 on all ortho-substituted benzoates that were tested. When 3,5-dichlorobenzoate was added as a cosubstrate with either 3- or 4-chlorobenzoate, cell yields and chloride release were greater than those observed from growth on either monochlorobenzoate alone. Moreover, resting cells of P111 grown on 4-chlorobenzoate released chloride from 3,5-dichlorobenzoate and produced no identifiable intermediate. In contrast, resting cells grown on 2,5-dichlorobenzoate metabolized 3,5-dichlorobenzoate without release of chloride and accumulated a degradation product, which was identified as 1-carboxy-1,2-dihydroxy-3,5-dichlorocyclohexadiene on the basis of gas chromatography-mass spectrometry confirmation of its two acid-hydrolyzed products, 3,5- and 2,4-dichlorophenol. Since 3,5-dichlorocatechol was rapidly metabolized by cells grown on 2,5-dichlorobenzoate, it is apparent that 1-carboxy-1,2-dihydroxy-3,5-dichlorocyclohexadiene is not further metabolized by these cells. Moreover, induction of a functional dihyrodiol dehydrogenase would not be required for growth of P111 on other ortho-chlorobenzoates since the corresponding chlorodihydrodiols produced from a 1,2-dioxygenase attack would spontaneously decompose to the corresponding catechols. In contrast, growth on 3-chloro-, 4-chloro-, or 3,5-dichlorobenzoate requires a functional dihydrodiol dehydrogenase, yet only the two monochlorobenzoates appear to induce for it.     

Metabolism of and inhibition by chlorobenzoates in Pseudomonas putida P111.

Pseudomonas putida P111 was isolated by enrichment culture on 2,5-dichlorobenzoate and was also able to grow on 2-chloro-, 3-chloro-, 4-chloro-, 2,3-dichloro-, 2,4-dichloro-, and 2,3,5-trichlorobenzoates. However, 3,5-dichlorobenzoate completely inhibited growth of P111 on all ortho-substituted benzoates that were tested. When 3,5-dichlorobenzoate was added as a cosubstrate with either 3- or 4-chlorobenzoate, cell yields and chloride release were greater than those observed from growth on either monochlorobenzoate alone. Moreover, resting cells of P111 grown on 4-chlorobenzoate released chloride from 3,5-dichlorobenzoate and produced no identifiable intermediate. In contrast, resting cells grown on 2,5-dichlorobenzoate metabolized 3,5-dichlorobenzoate without release of chloride and accumulated a degradation product, which was identified as 1-carboxy-1,2-dihydroxy-3,5-dichlorocyclohexadiene on the basis of gas chromatography-mass spectrometry confirmation of its two acid-hydrolyzed products, 3,5- and 2,4-dichlorophenol. Since 3,5-dichlorocatechol was rapidly metabolized by cells grown on 2,5-dichlorobenzoate, it is apparent that 1-carboxy-1,2-dihydroxy-3,5-dichlorocyclohexadiene is not further metabolized by these cells. Moreover, induction of a functional dihyrodiol dehydrogenase would not be required for growth of P111 on other ortho-chlorobenzoates since the corresponding chlorodihydrodiols produced from a 1,2-dioxygenase attack would spontaneously decompose to the corresponding catechols. In contrast, growth on 3-chloro-, 4-chloro-, or 3,5-dichlorobenzoate requires a functional dihydrodiol dehydrogenase, yet only the two monochlorobenzoates appear to induce for it.     

The Uptake of Growth Substances: VIII. ACCUMULATION OF CHLORINATED BENZOIC ACIDS BY AVENA SEGMENTS: A POSSIBLE MECHANISM FOR THE TRANSIENT PHASE OF ACCUMULATION

If segments from the mesocotyls of Avena sativa are first keptin buffer then the initial rates of uptake of radioactive 2,3,6-trichlorobenzoicacid (2,3,6-TCBA) and 2,4- and 2,5-dichlorobenzoic acids (2,4-DCBAand 2,5-DCBA) are less than those of freshly excised segments.No such effect of pretreatment is found for benzoic acid orfor 2-chlorobenzoic acid (2-CBA). Uptake of 2,3,6-TCBA normallybecomes negative between two and six hours after excision, andthis phase of net loss is prevented by the addition of streptomycin,which also offsets the decline in the rates of uptake of 2,5-DCBAand 2,4-DCBA. In contrast, streptomycin inhibits accumulationof 2-CBA. From a comparison of these results with similar andprior findings for substituted phenoxyacetic acids, it is concludedthat the initial uptake of 2,3,6-TCBA, 2,5-DCBA, and 2,4-DCBAis governed by an unstable accumulatory system (Type 1), whosebreakdown can result either in a phase of net loss during thecourse of uptake, or in a decline in uptake following pretreatment. Net loss of 2,3,6-TCBA is also prevented by synthalin (decamethylenediguanidine dihydrochloride), cetyl trimethyl ammonium bromide(CTAB) and by 2,3,5-triiodobenzoic acid (TIBA). During pretreatment,the presence of streptomycin, synthalin or TIBA prevents a fallin the subsequent uptake of 2,3,6-TCBA, while the addition ofCTAB causes a dramatic increase in uptake. We have proposed for Type 1 accumulation a biochemical mechanismcapable of accounting for the unstable nature of the accumulationand for the protective action of the compounds with cationicnitrogen groups, such as streptomycin, synthalin, and CTAB.     

Reductive dechlorination of 2,4-dichlorobenzoate to 4-chlorobenzoate and hydrolytic dehalogenation of 4-chloro-, 4-bromo-, and 4-iodobenzoate by Alcaligenes denitrificans NTB-1

Alcaligenes denitrificans NTB-1, previously isolated on 4-chlorobenzoate, also utilized 4-bromo-, 4-iodo-, and 2,4-dichlorobenzoate but not 4-fluorobenzoate as a sole carbon and energy source. During growth, stoichiometric amounts of halide were released. Experiments with whole cells and cell extracts revealed that 4-bromo- and 4-iodobenzoate were metabolized like 4-chlorobenzoate, involving an initial hydrolytic dehalogenation yielding 4-hydroxybenzoate, which in turn was hydroxylated to 3,4-dihydroxybenzoate. The initial step in the metabolism of 2,4-dichlorobenzoate was catalyzed by a novel type of reaction for aerobic organisms, involving inducible reductive dechlorination to 4-chlorobenzoate. Under conditions of low and controlled oxygen concentrations, A. denitrificans NTB-1 converted all 4-halobenzoates and 2,4-dichlorobenzoate almost quantitatively to 4-hydroxybenzoate.     

Reductive dechlorination of 2,4-dichlorobenzoate to 4-chlorobenzoate and hydrolytic dehalogenation of 4-chloro-, 4-bromo-, and 4-iodobenzoate by Alcaligenes denitrificans NTB-1.

Alcaligenes denitrificans NTB-1, previously isolated on 4-chlorobenzoate, also utilized 4-bromo-, 4-iodo-, and 2,4-dichlorobenzoate but not 4-fluorobenzoate as a sole carbon and energy source. During growth, stoichiometric amounts of halide were released. Experiments with whole cells and cell extracts revealed that 4-bromo- and 4-iodobenzoate were metabolized like 4-chlorobenzoate, involving an initial hydrolytic dehalogenation yielding 4-hydroxybenzoate, which in turn was hydroxylated to 3,4-dihydroxybenzoate. The initial step in the metabolism of 2,4-dichlorobenzoate was catalyzed by a novel type of reaction for aerobic organisms, involving inducible reductive dechlorination to 4-chlorobenzoate. Under conditions of low and controlled oxygen concentrations, A. denitrificans NTB-1 converted all 4-halobenzoates and 2,4-dichlorobenzoate almost quantitatively to 4-hydroxybenzoate.     

Mineralization of the herbicide 2,3,6-trichlorobenzoic acid by a co-culture of anaerobic and aerobic bacteria

Abstract Bacteria from an anaerobic enrichment reductively removed chlorine from the ortho- position of 2,3,6-trichlorobenzoic acid (2,3,6-TBA) producing 2,5-dichlorobenzoate (2,5-DBA). The strictly aerobic bacterium Pseudomonas aeruginosa JB2 subsequently used 2,5-DBA as a growth substrate in the presence of oxygen. The anaerobic dechlorinating microbial population was grown with P. aeruginosa JB2 in continuous culture. Inside the liquid culture, a nylon netting, on a stainless-steel support, contained vermiculite particles to provide a strictly anaerobic environment within the aerated culture. Complete mineralization of 2,3,6-TBA depended on the extent of oxygen input into the reactor. Under strictly anaerobic conditions 2,5-DBA and Cl⁻ were produced stoichiometrically through the reductive dechlorination of 2,3,6-TBA. This process of reductive dechlorination was not inhibited by (moderate) aeration resulting in an O₂-concentration of 0.3–0.5 μM in the culture liquid.     

Mineralization of the herbicide 2,3,6-trichlorobenzoic acid by a co-culture of anaerobic and aerobic bacteria

Abstract Bacteria from an anaerobic enrichment reductively removed chlorine from the ortho - position of 2,3,6-trichlorobenzoic acid (2,3,6-TBA) producing 2,5-dichlorobenzoate (2,5-DBA). The strictly aerobic bacterium Pseudomonas aeruginosa JB2 subsequently used 2,5-DBA as a growth substrate in the presence of oxygen. The anaerobic dechlorinating microbial population was grown with P. aeruginosa JB2 in continuous culture. Inside the liquid culture, a nylon netting, on a stainless-steel support, contained vermiculite particles to provide a strictly anaerobic environment within the aerated culture. Complete mineralization of 2,3,6-TBA depended on the extent of oxygen input into the reactor. Under strictly anaerobic conditions 2,5-DBA and Cl⁻ were produced stoichiometrically through the reductive dechlorination of 2,3,6-TBA. This process of reductive dechlorination was not inhibited by (moderate) aeration resulting in an O₂-concentration of 0.3–0.5 μM in the culture liquid.     

Preliminary characterization of four 2-chlorobenzoate-degrading anaerobic bacterial consortia

Dechlorination was the initial step of 2CB biodegradation in four 2-chlorobenzoate-degrading methanogenic consortia. Selected characteristics of ortho reductive dehalogenation were examined in consortia developed from the highest actively dechlorinating dilutions of the original 2CB consortia, designated consortia M34-9, P20-9, P21-9 and M50-7. In addition to 2-chlorobenzote, all four dilution consortia dehalogenated 4 of 32 additional halogenated aromatic substrates tested, including 2-bromobenzoate; 2,6-dichlorobenzoate; 2,4-dichlorobenzoate; and 2-chloro-5-hydroxybenzoate. Dehalogenation occurred exclusively at the ortho position. Both ortho chlorines were removed from 2,6-dichlorobenzoate. Benzoate was detected from 2-bromobenzoate and 2,6-dichlorobenzoate. 4-Chlorobenzoate and 3-hydroxybenzoate were formed from 2,4-dichlorobenzoate and 2-chloro-5-hydroxybenzoate, respectively. Only benzoate was further degraded. Slightly altering the structure of the parent 'benzoate molecule' resulted in observing reductive biotransformations other than dehalogenation. 2-Chlorobenzaldehyde was reduced to 2-chlorobenzyl alcohol by all four consortia. 2-chloroanisole was O-demethoxylated by three of the four consortia forming 2-chlorophenol. GC-MS analysis indicated reduction of the double bond in the propenoic side chain of 2-chlorocinnamate forming 2-chlorohydrocinnamate. None of the reduction products was dechlorinated. The following were not dehalogenated: 3- and 4-bromobenzoate; 3- and 4-chlorobenzoate; 2-, 3-, and 4-fluorobenzoate; 2-, 3-, and 4-iodobenzoate; 2-, 3-, and 4-chlorophenol; 2-chloroaniline; 2-chloro-5-methylbenzoate; 2,3-dichlorobenzoate; 2,5-dichlorobenzoate; 2,4,5-trichlorophenoxyacetic acid; and 2,4-dichlorophenoxyacetic acid. Consortia M34-9, P20-9, P21-9, and M50-7 dechlorinated 2-chlorobenzoate at 4 mm. Dechlorination rates were highest for consortia P20-9 followed by those of M50-7with rates declining above 2 and 3mm 2CB, respectively. The major physiological types of microorganisms in consortia M34-9, P20-9, P21-9, and M50-7 were sulfate-reducing and hydrogen-utilizing anaerobes.     

Degradation of chlorosubstituted aromatic compounds by Pseudomonas sp. strain B13: fate of 3,5-dichlorocatechol

The degradation of 3,5-dichlorocatechol by enzymes of 3-chlorobenzoate-grown cells of Pseudomonas sp. strain B13 was studied. The following compounds were formed from 3,5-dichlorocatechol: trans-2-chloro-4-carboxymethylenebut-2-en-4-olide, cis-2-chloro-4-carboxymethylenebut-2-en-4-olide, and chloroacetylacrylate as the decarboxylation product of 2-chloromaleylacetate. They were identified by chromatographic and spectroscopic methods (UV, MS, PMR). An enzyme activity converting trans-2-chloro-4-carboxymethylenebut-2-en-4-olide into the cis-isomer was observed.Abbreviations 3CB 3-chlorobenzoate - 4CB 4-chlorobenzoate - 3,5DCB 3,5-dichlorobenzoate - 2,4D 2,4-dichlorophenoxyacetate - NOE Nuclear-Overhauser-Effect     

The Uptake of Growth Substances: VII. THE ACCUMULATION OF CHLORINATED BENZOIC ACIDS BY STEM TISSUES2

The courses of uptake of benzoic acid (BA) and its 2-chloro-(2-CBA), 2,4-dichloro- (2,4-DCBA), 2,5-dichloro- (2,5-DCBA),and 2,3,6-trichloro- (2,3,6-TCBA) derivatives, all containing¹⁴C in the carboxyl group, have been investigated, employingstem segments of Pisum sativum, Gossypium hirsutum, and Avenasativa. From comparisons of the rates of accumulation by segmetns ofdifferent length it is conclueded that for each compound uptakeproceeds largely or wholly via the cut surfaces. The initial uptake of BA and 2-CBA by segments of Pisum is depressedas the pH of the solution is raised from 4 to 6.5, but the fallis less rapid than the decrease in the proportion of undissociatedmolecules. For all three species, BA and 2-CBA, which induced no extensiongrowth, were accumulated at a more or less constant rate. Bycontrast, the course of uptake of 2,3,6-TCBA, a powerful auxin,exhibited marked deviations from a linear pattern, especiallyin Avena where uptake became negative between four and six hours.This loss of radioactivity from the tissues was due to the netegress of 2,3,6-TCBA itself into the external solution. In Avenathe two dichloro-benzoic acids (2,4-DCBA and 2,5-DCBA) haveintermediate trens: net accumulation declined almost to zerobut subsequently recovered and proceeded at a rapid rate. These findings are discussed in relation to prior studies ofthe uptake of substituted phenoxyacetic acids and the conceptsof Type 1 and Type 2 accumulation. It is proposed that accumulationof BA and 2-CBA is largely governed by a stable Type 2 processwhile the initial uptake of the powerful auxins, 2,3,6-TCBAand 2,5-DCBA proceeds via an unstable system, similar or identicalto Type 1 accumulation.     

Kinetics and Extent of Mineralization of Organic Chemicals at Trace Levels in Freshwater and Sewage

A sensitive and rapid method was developed to measure the mineralization of ¹⁴C-labeled organic compounds at picogram-per-milliliter or lower levels in samples of natural waters and sewage. Mineralization was considered to be equivalent to the loss of radioactivity from solutions. From 93 to 98% of benzoate, benzylamine, aniline, phenol, and 2,4-dichlorophenoxyacetate at one or more concentrations below 300 ng/ml was mineralized in samples of lake waters and sewage, indicating little or no incorporation of carbon into microbial cells. Assimilation of ¹⁴C by the cells mineralizing benzylamine in lake water was not detected. Mineralization in lake waters was linear with time for aniline at 5.7 pg to 500 ng/ml, benzylamine at 310 ng/ml, phenol at 102 fg to 10 mg/ml, 2,4-dichlorophenoxyacetate at 1.5 pg/ml, and di-(2-ethylhexyl) phthalate at 21 pg to 200 ng/ml, but it was exponential at several p-nitrophenol concentrations. The rate of mineralization of 50 and 500 ng of aniline per ml and 200 pg and 2.0 ng of the phthalate per ml increased with time in lake waters. The phthalate and 2,4-dichlorophenoxyacetate were mineralized in samples from a eutrophic but not an oligotrophic lake. Addition to eutrophic lake water of a benzoate-utilizing bacterium did not increase the rate of benzoate mineralization at 34 and 350 pg/ml but did so at 5 and 50 ng/ml. Glucose and phenol reduced the percentage of p-nitrophenol mineralized at p-nitrophenol concentrations of 200 ng/ml but not at 22.6 pg/ml and inhibited the rates of mineralization at both concentrations. These results show that the kinetics of mineralization, the capacity of the aquatic community to assimilate carbon from the substrate or the extent of assimilation, and the sensitivity of the mineralizing populations to organic compounds are different at trace levels than at higher concentrations of organic compounds.     

Effect of chlorine substitution on the bacterial metabolism of various polychlorinated biphenyls.

Of 36 pure isomers (chlorine numbers 1 to 5) of polychlorinated biphenyls examined, 23 compounds were metabolized by Alcaligenes sp. strain Y42, and 33 compounds were metabolized by Acinetobacter sp. strain P6. The major pathway of many polychlorinated biphenyl isomers examined was considered to proceed through 2',3'-dihydro-2',3'-diol compounds, concomitant dehydrogenated 2',3'-dihydroxy compounds, subsequently the 1',2'-meta-cleavage compounds (chlorinated derivatives of 2-hydroxy-6-oxo-6-phenylhexa-2,4-dienoic acids), and then chlorobenzoic acids. The meta-cleavage products were usually converted to chlorobenzoic acids upon further incubation in many polychlorinated biphenyls, but they accumulated specifically in the metabolism of 2,4'-, 2,4,4'-, and 2,5,4'-chlorobiphenyls, which are all chlorinated at the 2,4'-position in the molecules in common. Dihydroxy compounds accumulated mainly in the metabolism of 2,6-, 2,3,6-, 2,4,2',5'-, 2,5,2',5'-, and 2,4,5,2',5'-chlorobiphenyls by Acinetobacter sp. P6. The 2,3,2',3'-, 2,3,2',5'-, and 2,4,5,2',3'-chlorobiphenyls, which are chlorinated at the 2,3-position of one of the rings, were metabolized in a different fashion. Two major metabolites of a chlorobenzoic acid and an unknown compound accumulated always in the metabolism of this group of polychlorinated biphenyls. 2,4,6-Trichlorobiphenyl was metabolized quite differently between the two organisms. Alcaligenes sp. Y42 metabolized this compound very slowly to trichlorobenzoic acid by the major oxidative route. In contrast, Acinetobacter sp. P6 metabolized it to a trihydroxy compound via a dihydroxy compound.     

NADPH-dependent reductive ortho dehalogenation of 2,4-dichlorobenzoic acid in Corynebacterium sepedonicum KZ-4 and Coryneform bacterium strainNTB-1 via 2,4-dichlorobenzoyl coenzyme A.

Corynebacterium sepedonicum KZ-4, described earlier as a strain capable of growth on 2,4-dichlorobenzoate (G.M. Zaitsev and Y.N. Karasevich, Mikrobiologiya 54:356-369, 1985), is known to metabolize this substrate via 4-hydroxybenzoate and protocatechuate, and evidence consistent with an initial reductive dechlorination step to form 4-chlorobenzoate was found in another coryneform bacterium, strain NTB-1 (W.J.J. van den Tweel, J.B. Kok, and J.A.M. de Bont, Appl. Environ. Microbiol. 53:810-815, 1987). 2-Chloro-4-fluorobenzoate was found to be converted stoichiometrically to 4-fluorobenzoate by resting cells of strain KZ-4, compatible with a reductive process. Experiments with cell extracts demonstrated that Mg - ATP and coenzyme A (CoA) were required to stimulate reductive dehalogenation, consistent with the intermediacy of 2-chloro-4-fluoro-benzoyl-CoA and 2,4-dichlorobenzoyl-CoA thioesters. 2,4-Dichlorobenzoyl-CoA was shown to be converted to 4-chlorobenzoyl-CoA in a novel NADPH-dependent reaction in extracts of both KZ-4 and NTB-1. In addition to the ligase and reductive dehalogenase activities, hydrolytic 4-chlorobenzoyl-CoA dehalogenase and thioesterase activities, 4-hydroxybenzoate 3-monooxygenase, and protocatechuate 3,4-dioxygenase activities were demonstrated to be present in the soluble fraction of KZ-4 extracts following ultracentrifugation. We propose that the pathway for 2,4-dichlorobenzoate catabolism in strains KZ-4 and NTB-1 involves formation of 2,4-dichlorobenzoyl-CoA, NADPH-dependent ortho dehalogenation yielding 4-chlorobenzoyl-CoA, hydrolytic removal of chlorine from the para position to generate 4-hydroxybenzoyl-CoA, hydrolysis to form 4-hydroxybenzoate, oxidation to yield protocatechuate, and oxidative ring cleavage.     

Effect of chlorine substitution on the bacterial metabolism of various polychlorinated biphenyls.

Of 36 pure isomers (chlorine numbers 1 to 5) of polychlorinated biphenyls examined, 23 compounds were metabolized by Alcaligenes sp. strain Y42, and 33 compounds were metabolized by Acinetobacter sp. strain P6. The major pathway of many polychlorinated biphenyl isomers examined was considered to proceed through 2',3'-dihydro-2',3'-diol compounds, concomitant dehydrogenated 2',3'-dihydroxy compounds, subsequently the 1',2'-meta-cleavage compounds (chlorinated derivatives of 2-hydroxy-6-oxo-6-phenylhexa-2,4-dienoic acids), and then chlorobenzoic acids. The meta-cleavage products were usually converted to chlorobenzoic acids upon further incubation in many polychlorinated biphenyls, but they accumulated specifically in the metabolism of 2,4'-, 2,4,4'-, and 2,5,4'-chlorobiphenyls, which are all chlorinated at the 2,4'-position in the molecules in common. Dihydroxy compounds accumulated mainly in the metabolism of 2,6-, 2,3,6-, 2,4,2',5'-, 2,5,2',5'-, and 2,4,5,2',5'-chlorobiphenyls by Acinetobacter sp. P6. The 2,3,2',3'-, 2,3,2',5'-, and 2,4,5,2',3'-chlorobiphenyls, which are chlorinated at the 2,3-position of one of the rings, were metabolized in a different fashion. Two major metabolites of a chlorobenzoic acid and an unknown compound accumulated always in the metabolism of this group of polychlorinated biphenyls. 2,4,6-Trichlorobiphenyl was metabolized quite differently between the two organisms. Alcaligenes sp. Y42 metabolized this compound very slowly to trichlorobenzoic acid by the major oxidative route. In contrast, Acinetobacter sp. P6 metabolized it to a trihydroxy compound via a dihydroxy compound.     

Role of chemical concentration and second carbon sources in acclimation of microbial communities for biodegradation

A study was conducted to determine the role of concentration of the test chemical, of a second organic compound, and of mutation in the acclimation period before the mineralization of organic compounds in sewage. The acclimation period for the mineralization in sewage of 2 micrograms of 4-nitrophenol (PNP) per liter increased from 6 to 12 days in the presence of 10 mg of 2,4-dinitrophenol per liter. The extension of the acclimation period was equivalent to the time required for mineralization of 2,4-dinitrophenol. In contrast, the time for acclimation for the degradation of 2 micrograms of PNP per liter was reduced when 10 or 100 mg of phenol per liter was added. Lower phenol levels increased the acclimation period to 8 days. The length of the acclimation period for PNP mineralization decreased as the initial concentration of PNP increased from 2 micrograms to 100 mg/liter. The acclimation period for phenol mineralization was lengthened as the phenol concentration increased from 100 to 1,400 mg/liter. The length of the acclimation period for PNP and phenol biodegradation was reproducible, but it varied among replicates for the biodegradation of other nitro-substituted compounds added to sewage or lake water, suggesting that a mutation was responsible for acclimation to these other compounds. The acclimation period may thus reflect the time required for the destruction of toxins, and it also may be affected by the concentration of the test compound or the presence of other substrates.     

Role of chemical concentration and second carbon sources in acclimation of microbial communities for biodegradation.

A study was conducted to determine the role of concentration of the test chemical, of a second organic compound, and of mutation in the acclimation period before the mineralization of organic compounds in sewage. The acclimation period for the mineralization in sewage of 2 micrograms of 4-nitrophenol (PNP) per liter increased from 6 to 12 days in the presence of 10 mg of 2,4-dinitrophenol per liter. The extension of the acclimation period was equivalent to the time required for mineralization of 2,4-dinitrophenol. In contrast, the time for acclimation for the degradation of 2 micrograms of PNP per liter was reduced when 10 or 100 mg of phenol per liter was added. Lower phenol levels increased the acclimation period to 8 days. The length of the acclimation period for PNP mineralization decreased as the initial concentration of PNP increased from 2 micrograms to 100 mg/liter. The acclimation period for phenol mineralization was lengthened as the phenol concentration increased from 100 to 1,400 mg/liter. The length of the acclimation period for PNP and phenol biodegradation was reproducible, but it varied among replicates for the biodegradation of other nitro-substituted compounds added to sewage or lake water, suggesting that a mutation was responsible for acclimation to these other compounds. The acclimation period may thus reflect the time required for the destruction of toxins, and it also may be affected by the concentration of the test compound or the presence of other substrates.     

Synthesis of certain 2'-deoxyuridine derivatives containing substituted phenoxy groups attached to C-5'; evaluation as potential dUTP analogues

Derivatives of 2'-deoxyuridine in which the 5'-OH group is replaced by a 2,3,6-trifluoro-5-hydroxy-4-nitrophenoxy or a 4-carboxy-2,3,6-trifluoro-5-hydroxyphenoxy group have been prepared for evaluation as possible dUTP analogues. They showed a weak ability to displace radiolabelled dUTP from a dUTP-binding antiserum. The corresponding compounds lacking the three fluorine substituents were prepared for comparison.     

SYNTHESIS OF CERTAIN 2′-DEOXYURIDINE DERIVATIVES CONTAINING SUBSTITUTED PHENOXY GROUPS ATTACHED TO C-5′; EVALUATION AS POTENTIAL dUTP ANALOGUES

Derivatives of 2′-deoxyuridine in which the 5′-OH group is replaced by a 2,3,6-trifluoro-5-hydroxy-4-nitrophenoxy or a 4-carboxy-2,3,6-trifluoro-5-hydroxyphenoxy group have been prepared for evaluation as possible dUTP analogues. They showed a weak ability to displace radiolabelled dUTP from a dUTP-binding antiserum. The corresponding compounds lacking the three fluorine substituents were prepared for comparison.