The role of exogenous electron donors for accelerating 2,4,6-trichlorophenol biotransformation and mineralization

2,4,6-Trichlorophenol (TCP) is a biologically recalcitrant compound, but its biodegradation via reductive dechlorination can be accelerated by adding an exogenous electron donor. In this work, acetate and formate were evaluated for their ability to accelerate TCP reductive dechlorination, as well to accelerate mono-oxygenation of TCP’s reduction product, phenol. Acetate and formate accelerated TCP reductive dechlorination, and the impact was proportional to the number of electron equivalents released by oxidation of the donor: 8 e^? equivalents per mol for acetate, compared to 2 e^? eq per mol for formate. The acceleration phenomenon was similar for phenol mono-oxygenation, and this increased the rate of TCP mineralization. Compared to endogenous electron equivalents generated by phenol mineralization, the impact of exogenous electron donor was stronger on a per-equivalent basis.     

How UV photolysis accelerates the biodegradation and mineralization of sulfadiazine (SD)

Sulfadiazine (SD), one of broad-spectrum antibiotics, exhibits limited biodegradation in wastewater treatment due to its chemical structure, which requires initial mono-oxygenation reactions to initiate its biodegradation. Intimately coupling UV photolysis with biodegradation, realized with the internal loop photobiodegradation reactor, accelerated SD biodegradation and mineralization by 35 and 71 %, respectively. The main organic products from photolysis were 2-aminopyrimidine (2-AP), p-aminobenzenesulfonic acid (ABS), and aniline (An), and an SD-photolysis pathway could be identified using C, N, and S balances. Adding An or ABS (but not 2-AP) into the SD solution during biodegradation experiments (no UV photolysis) gave SD removal and mineralization rates similar to intimately coupled photolysis and biodegradation. An SD biodegradation pathway, based on a diverse set of the experimental results, explains how the mineralization of ABS and An (but not 2-AP) provided internal electron carriers that accelerated the initial mono-oxygenation reactions of SD biodegradation. Thus, multiple lines of evidence support that the mechanism by which intimately coupled photolysis and biodegradation accelerated SD removal and mineralization was through producing co-substrates whose oxidation produced electron equivalents that stimulated the initial mono-oxygenation reactions for SD biodegradation.     

Biodegradation of pyridine by an isolated bacterial consortium/strain and bio-augmentation of strain into activated sludge to enhance pyridine biodegradation

Pyridine and pyridine based products are of major concern as environmental pollutants due to their recalcitrant, persistent, toxic and teratogenic nature. In this study, we describe biodegradation of pyridine by an isolated consortium/strain under aerobic condition. Batch experiment results reveal that at lower initial pyridine concentrations (1-20 mg l(-1)), almost complete degradation was observed whereas at higher concentration (30-50 mg l(-1)), the degradation efficiency was dropped significantly. This may be due to inhibitory effect of pyridine at higher concentrations. The value of decay and yield coefficient was also determined. Furthermore, the bio-augmentation of isolated consortium/strain into the activated sludge consortium in different quantity has been also done and the effect of bio-augmentation on degradation has been studied. The results reveal that as the quantity of bio-augmentation increases, the degradation of pyridine increases. At 25% bio-augmentation, complete degradation of 20 mg l(-1) of pyridine can be achieved within 96 h of incubation. Thus, the study concluded that the bio-augmentation of the isolated consortium/strain into the sludge enhances the pyridine degradation efficiency of the biomass.     

The effect of pyridine and pyridine-N-oxide on the monooxygenase system of rat liver microsomes]

Effects of pyridine and pyridine-N-oxide on the monooxygenase system of rat liver microsomes have been studied. Pyridine (200 mg/kg) increased total cytochrome P-450 content and activated metabolism of some specific substrates 24 hours after injection. There was an increase in the degree of p-nitrophenol and chlorzoxazone hydroxylation due to increasing ethanol-induced cytochrome P-450IIE1 content. Pyridine was also able to induce cytochrome P-450IIB1 in rat microsomes; this reaction was accompanied by acceleration of 7-pentoxyresorufin 0-dealkylation. Cytochrome P-450IA1 appearance in liver microsomes was associated with increasing content of cytochrome P-450IA2. Dealkylation rates for specific substrates (7-ethoxyresorufin and 7-methoxyresorufin) were also increased. Similar to pyridine, pyridine-7-oxide induced cytochromes P-450IIE1, P-450IIB1/B2, and P-450IA1/A2, resulting in activation of specific substrate metabolism. Hence, pyridine and its derivative pyridine-N-oxide can be regarded as effective inducers of cytochrome P-450.     

Biodegradation of pyridine in a completely mixed activated sludge process

A potential bacterial culture (P1), isolated from garden soil and identified as Pseudomonas pseudoalcaligenes-KPN, was used as a starter seed to develop the biomass in a completely mixed activated sludge (CMAS) reactor and the system was evaluated for treatment of wastewater containing pyridine. The results of this study indicate that pyridine could be degraded efficiently at a loading of 0.251 kg pyridine kg MLSS(-1) d(-1) (0.156 kg TOC kg MLSS(-1) d(-1)) and at an optimal hydraulic retention time (HRT) of 24 h. Pyridine was used as the sole source of carbon and nitrogen by the biomass. Ammonia-nitrogen (NH3-N) was formed due to the metabolism of the pyridine ring. In the present investigation, the performance of CMAS with reference to pyridine biodegradation and the bio-kinetic constants for the biodegradation of pyridine, in a continuous system, were computed. The results indicate that a CMAS system inoculated with P. pseudoalcaligenes-KPN, under optimum conditions of HRT and pyridine loading, gives a yield coefficient of (Y) 0.29, decay coefficient (Kd) 0.0011 d(-1), maximum growth rate constant (mumax) 0.108 d(-1) and saturation rate constant (Ks) 5.37 mg L(-1) for pyridine.     

Influence of phenol on the biodegradation of pyridine by freely suspended and immobilized Pseudomonas putida MK1

AIMS: To study the effect of co-contaminants (phenol) on the biodegradation of pyridine by freely suspended and calcium alginate immobilized bacteria. METHODS AND RESULTS: Varying concentrations of phenol were added to free and calcium alginate immobilized Pseudomonas putida MK1 (KCTC 12283) to examine the effect of this pollutant on pyridine degradation. When the concentration of phenol reached 0.38 g l(-1), pyridine degradation by freely suspended bacteria was inhibited. The increased inhibition with the higher phenol levels was apparent in increased lag times. Pyridine degradation was essentially completely inhibited at 0.5 g l(-1) phenol. However, immobilized cells showed tolerance against 0.5 g l(-1) phenol and pyridine degradation by immobilized cell could be achieved. CONCLUSIONS: This works shows that calcium alginate immobilization of microbial cells can effectively increase the tolerance of P. putida MK1 to phenol and results in increased degradation of pyridine. SIGNIFICANCE AND IMPACT OF THE STUDY: Treatment of wastewater stream can be negatively affected by the presence of co-pollutants. This work demonstrates the potential of calcium alginate immobilization of microbes to protect cells against compound toxicity resulting in an increase in pollutant degradation.     

密粘褶菌Gloeophyllum trabeum胞外低分子量多肽的分离纯化及其对纤维素生物降解作用

通过HPLC高效液相层析由褐腐真菌中能强烈降解木质纤维素的代表菌株密粘褶菌Gloeo phyllumtrabeum的胞外培养液 ,分离纯化得到一低分子量的活性多肽组分 (Gt因子 ) .Gt因子具有较好热稳定性 ,在pH 2 5～ 6 5范围内保持稳定 .Gt因子分子量在 4 0 0 0左右 ,等电点pI 6 6 .Gt因子具有络合Fe3 + 的能力 ,且能够将Fe3 + 还原为Fe2 + .在O2 存在时 ,能以纤维素物质为电子供体形成羟基自由基HO·.利用循环伏安法 ,观察到Gt因子与纤维素底物之间的氧化还原过程 .研究表明 ,Gt因子极有可能在褐腐菌的纤维素降解初期起着重要的作用 .     

An NAD(P) reductase derived from Chlorobium thiosulfa-tophilum: Purification and some properties

A highly purified preparation of an NAD(P) reductase was obtained from Chlorobium thiosulfatophilum and some of its properties were studied. The enzyme possesses FAD as the prosthetic group, and reduces benzyl viologen, 2,6-dichloro-phenolindophenol and cytochromes c, including cytochrome c-555 (C. thiosulfato-philum), with NADPH or NADH as the electron donor. It reduces NADP⁺ or NAD⁺ photosynthetically with spinach chloroplasts in the presence of added spinach ferredoxin. It reduces the pyridine nucleotides with reduced benzyl viologen. The enzyme also shows a pyridine nucleotide transhydrogenase activity. In these reactions, the type of pyridine nucleotide (NADP or NAD) which functions more efficiently with the enzyme varies with the concentration of the nucleotide used; at concentrations lower than approx. 1.0 mM, NADPH (or NADP⁺) is better electron donor (or acceptor), while NADH (or NAD⁺) is a better electron donor (or acceptor) at concentrations higher than approx. 1.0 mM. Reduction of dyes or cytochromes c catalysed by the enzyme is strongly inhibited by NADP⁺, 2′-AMP and and atebrin.     

以N-甲基吡咯烷酮(NMP)为电子供体进行反硝化的可行性及实验研究

【目的】利用N-甲基吡咯烷酮(N-methylpyrrolidone, NMP)作为电子供体进行反硝化实验,以实现废水资源化。【方法】分别将NMP废水和葡萄糖作为电子供体加入到模拟的城市污水处理尾水中进行反硝化,比较2种电子供体去除硝酸盐的规律。同时考查NMP在反硝化过程中的氮素释放规律,并对所释放的氮素进行后续处理。最后再对它们作为电子供体时的反硝化污泥采用高通量测序,从微生物群落的角度分析NMP作为电子供体时其作用机理是否相同。【结果】当以NMP为电子供体时,硝酸盐氮的去除速率比葡萄糖为电子供体时要快67%。在8 h的反硝化结束后,剩余的硝酸盐氮、累积的亚硝酸盐氮和NMP本身所释放氨氮之和的总氮,与葡萄糖为电子供体时相近。【结论】NMP废水可以作为电子供体用于城镇污水处理厂的深度脱氮。对2种碳源所驯化的反硝化污泥样品进行高通量分析表明,NMP与葡萄糖作为电子供体用于反硝化反应时,相关的作用机理是不同的。该项研究结果对利用含氮杂环化合物作为电子供体进行反硝化具有重要的理论指导意义。     

Microbial transformation of ethylpyridines

Pyridine and its derivatives have been found as pollutants in the environment. Although alkylpyridines constitute the largest class of pyridines contaminating the environment, little information is available concerning the fate and transformation of these compounds. In this investigation ethylpyridines have been used as model compounds for investigating the biodegradability of alkylpyridines. A mixed culture of ethylpyridine-degrading microorganisms was obtained from a soil that had been exposed to a variety of pyridine derivatives for several decades. The enrichment culture was able to degrade 2-, 3-, and 4-ethylpyridine (100 mg/L) at 28° C and pH 7 within two weeks under aerobic conditions. The degradation rate was greatest for 2-ethylpyridine and least for 3-ethylpyridine. Transformation of ethylpyridines was dependent on substrate concentration, pH, and incubation temperature. Studies on the metabolic pathway of 4-ethylpyridine revealed two products; these chemicals were identified by MS and NMR analyses as 4-ethyl-2(1H)-pyridone and 4-ethyl-2-piperidone. 6-Ethyl-2(1H)-pyridone was determined to be a product of 2-ethylpyridine degradation. These results indicate that the transformation mechanism of ethylpyridines involves hydroxylation and reduction of the aromatic ring before ring cleavage.     

Reactive red azo dye degradation in a UASB bioreactor: Mechanism and kinetics

Textile industry uses azo dyes in its processes, which are complex organic molecules that are not easy to be degraded. Reactive dyes are especially difficult to remove from wastewater because of the characteristics of the molecule: one or more azo bonds, naphthalene‐disulfonate, triazine or chloro‐triazine, and phenyl‐amine groups. The degradation of the azo dye reactive red 272 was studied under anaerobic conditions in a hybrid Upflow Anaerobic Sludge Bed reactor (UASB) with an activated carbon bed. An adapted consortium of microorganisms was used in the kinetic study (batch) and to inoculate the UASB reactor. The experimental design identified the main factors determining the dye reduction efficiency are the initial concentration of dye and dextrose (as electron donor) and the residence time in the reactor. Dye reduction rate was decreased as the concentration increases in the wastewater; as a result, a kinetic model with a change from first to second order is proposed. The kinetic study showed that the process is first abiotic (adsorption) and then biotic (biodegradation).     

Electron transfer complex between nitrous oxide reductase and cytochrome c552 from Pseudomonas nautica: kinetic, nuclear magnetic resonance, and docking studies

The multicopper enzyme nitrous oxide reductase (N 2OR) catalyzes the final step of denitrification, the two-electron reduction of N 2O to N 2. This enzyme is a functional homodimer containing two different multicopper sites: CuA and CuZ. CuA is a binuclear copper site that transfers electrons to the tetranuclear copper sulfide CuZ, the catalytic site. In this study, Pseudomonas nautica cytochrome c 552 was identified as the physiological electron donor. The kinetic data show differences when physiological and artificial electron donors are compared [cytochrome vs methylviologen (MV)]. In the presence of cytochrome c 552, the reaction rate is dependent on the ET reaction and independent of the N 2O concentration. With MV, electron donation is faster than substrate reduction. From the study of cytochrome c 552 concentration dependence, we estimate the following kinetic parameters: K m c 552 = 50.2 +/- 9.0 muM and V max c 552 = 1.8 +/- 0.6 units/mg. The N 2O concentration dependence indicates a K mN 2 O of 14.0 +/- 2.9 muM using MV as the electron donor. The pH effect on the kinetic parameters is different when MV or cytochrome c 552 is used as the electron donor (p K a = 6.6 or 8.3, respectively). The kinetic study also revealed the hydrophobic nature of the interaction, and direct electron transfer studies showed that CuA is the center that receives electrons from the physiological electron donor. The formation of the electron transfer complex was observed by (1)H NMR protein-protein titrations and was modeled with a molecular docking program (BiGGER). The proposed docked complexes corroborated the ET studies giving a large number of solutions in which cytochrome c 552 is placed near a hydrophobic patch located around the CuA center.     

Structural characterization of a human cytosolic NMN/NaMN adenylyltransferase and implication in human NAD biosynthesis

Pyridine dinucleotides (NAD and NADP) are ubiquitous cofactors involved in hundreds of redox reactions essential for the energy transduction and metabolism in all living cells. In addition, NAD also serves as a substrate for ADP-ribosylation of a number of nuclear proteins, for silent information regulator 2 (Sir2)-like histone deacetylase that is involved in gene silencing regulation, and for cyclic ADP ribose (cADPR)-dependent Ca(2+) signaling. Pyridine nucleotide adenylyltransferase (PNAT) is an indispensable central enzyme in the NAD biosynthesis pathways catalyzing the condensation of pyridine mononucleotide (NMN or NaMN) with the AMP moiety of ATP to form NAD (or NaAD). Here we report the identification and structural characterization of a novel human PNAT (hsPNAT-3) that is located in the cytoplasm and mitochondria. Its subcellular localization and tissue distribution are distinct from the previously identified human nuclear PNAT-1 and PNAT-2. Detailed structural analysis of PNAT-3 in its apo form and in complex with its substrate(s) or product revealed the catalytic mechanism of the enzyme. The characterization of the cytosolic human PNAT-3 provided compelling evidence that the final steps of NAD biosynthesis pathways may exist in mammalian cytoplasm and mitochondria, potentially contributing to their NAD/NADP pool.     

Reduced flavins promote oxidative DNA damage in non-respiring Escherichia coli by delivering electrons to intracellular free iron

When cells are exposed to external H(2)O(2), the H(2)O(2) rapidly diffuses inside and oxidizes ferrous iron, thereby forming hydroxyl radicals that damage DNA. Thus the process of oxidative DNA damage requires only H(2)O(2), free iron, and an as-yet unidentified electron donor that reduces ferric iron to the ferrous state. Previous work showed that H(2)O(2) kills Escherichia coli especially rapidly when respiration is inhibited either by cyanide or by genetic defects in respiratory enzymes. In this study we established that these respiratory blocks accelerate the rate of DNA damage. The respiratory blocks did not substantially affect the amounts of intracellular free iron or H(2)O(2), indicating that that they accelerated damage because they increased the availability of the electron donor. The goal of this work was to identify that donor. As expected, the respiratory inhibitors caused a large increase in the amount of intracellular NADH. However, NADH itself was a poor reductant of free iron in vitro. This suggests that in non-respiring cells electrons are transferred from NADH to another carrier that directly reduces the iron. Genetic manipulations of the amounts of intracellular glutathione, NADPH, alpha-ketoacids, ferredoxin, and thioredoxin indicated that none of these was the direct electron donor. However, cells were protected from cyanide-stimulated DNA damage if they lacked flavin reductase, an enzyme that transfers electrons from NADH to free FAD. The K(m) value of this enzyme for NADH is much higher than the usual intracellular NADH concentration, which explains why its flux increased when NADH levels rose during respiratory inhibition. Flavins that were reduced by purified flavin reductase rapidly transferred electrons to free iron and drove a DNA-damaging Fenton system in vitro. Thus the rate of oxidative DNA damage can be limited by the rate at which electron donors reduce free iron, and reduced flavins become the predominant donors in E. coli when respiration is blocked. It remains unclear whether flavins or other reductants drive Fenton chemistry in respiring cells.     

Chloroform respiration to dichloromethane by a Dehalobacter population

Chloroform (CF), or trichloromethane, is an ubiquitous environmental pollutant because of its widespread industrial use, historically poor disposal and recalcitrance to biodegradation. Chloroform is a potent inhibitor of metabolism and no known organism uses it as a growth substrate. We discovered that CF was rapidly and sustainably dechlorinated in the course of investigating anaerobic reductive dechlorination of 1,1,1‐trichloroethane in a Dehalobacter‐containing culture. Like 1,1,1‐trichloroethane dechlorination in this culture, CF dechlorination was a growth‐linked respiratory process, requiring H₂ as an electron donor and CF as an electron acceptor. Moreover, the same specific reductive dehalogenase likely catalyzed both reactions. This Dehalobacter population appears specialized for substrates with three halogen substituents on the same carbon atom, with widespread implications for bioremediation.     

Biodegradability of chlorinated solvents and related chlorinated aliphatic compounds

The biodegradability of chlorinated methanes, chlorinated ethanes, chlorinated ethenes, chlorofluorocarbons (CFCs), chlorinated acetic acids, chlorinated propanoids and chlorinated butadienes was evaluated based on literature data. Evidence for the biodegradation of compounds in all of the compound categories evaluated has been reported. A broad range of chlorinated aliphatic structures are susceptible to biodegradation under a variety of physiological and redox conditions. Microbial biodegradation of a wide variety of chlorinated aliphatic compounds was shown to occur under five physiological conditions. However, any given physiological condition could only act upon a subset of the chlorinated compounds. Firstly, chlorinated compounds are used as an electron donor and carbon source under aerobic conditions. Secondly, chlorinated compounds are cometabolized under aerobic conditions while the microorganisms are growing (or otherwise already have grown) on another primary substrate. Thirdly, chlorinated compounds are also degraded under anaerobic conditions in which they are utilized as an electron donor and carbon source. Fourthly, chlorinated compounds can serve as an electron acceptor to support respiration of anaerobic microorganisms utilizing simple electron donating substrates. Lastly chlorinated compounds are subject to anaerobic cometabolism becoming biotransformed while the microorganisms grow on other primary substrate or electron acceptor. The literature survey demonstrates that, in many cases, chlorinated compounds are completely mineralised to benign end products. Additionally, biodegradation can occur rapidly. Growth rates exceeding 1 d^-1 were observed for many compounds. Most compound categories include chlorinated structures that are used to support microbial growth. Growth can be due to the use of the chlorinated compound as an electron donor or alternatively to the use of the chlorinated compound as an electron acceptor (halorespiration). Biodegradation linked to growth is important, since under such conditions, rates of degradation will increase as the microbial population (biocatalyst) increases. Combinations of redox conditions are favorable for the biodegradation of highly chlorinated structures that are recalcitrant to degradation under aerobic conditions. However, under anaerobic conditions, highly chlorinated structures are partially dehalogenated to lower chlorinated counterparts. The lower chlorinated compounds are subsequently more readily mineralized under aerobic conditions.     

Enhanced dimethyl phthalate biodegradation by accelerating phthalic acid di-oxygenation

The aerobic biodegradation of dimethyl phthalate (DMP) is initiated with two hydrolysis reactions that generate an intermediate, phthalic acid (PA), that is further biodegraded through a two-step di-oxygenation reaction. DMP biodegradation is inhibited when PA accumulates, but DMP’s biodegradation can be enhanced by adding an exogenous electron donor. We evaluated the effect of adding succinate, acetate, or formate as an exogenous electron donor. PA removal rates were increased by 15 and 30% for initial PA concentrations of 0.3 and 0.6 mM when 0.15 and 0.30 mM succinate, respectively, were added as exogenous electron donor. The same electron-equivalent additions of acetate and formate had the same acceleration impacts on PA removal. Consequently, the DMP-removal rate, even PA coexisting with DMP simultaneously, was accelerated by 37% by simultaneous addition of 0.3 mM succinate. Thus, lowering the accumulation of PA by addition of an electron increased the rate of DMP biodegradation.     

Yeast glutathione reductase. Steady-state kinetic studies of its transhydrogenase activity.

Yeast glutathione reductase catalyzes a pyridine nucleotide transhydrogenase reaction using either NADPH or NADH as the electron donor and thionicotinamideadenine dinucleotide phosphate as the electron acceptor. Competitive substrate inhibition of the transhydrogenase reaction by NADPH (K_i = 11 μM) is observed when NADPH is the electron donor. Competitive substrate inhibition by thionicotinamide-adenine dinucleotide phosphate (K_i = 58 μM) is observed with NADH as the electron donor. The turnover numbers of the two transhydrogenase reactions are similar and are equal to about 1% of the turnover number for the NADPH-dependent reduction of oxidized glutathione catalyzed by the enzyme. The transhydrogenase kinetics are analyzed in terms of a pingpong mechanism. It is concluded that the substrate inhibition results from formation of abortive complexes of NADPH with the reduced form of the enzyme and of thionicotinamide-adenine dinucleotide phosphate with the oxidized form of the enzyme. With NADPH as the electron donor, the apparent Michaelis constant for thionicotinamide-adenine dinucleotide phosphate is sensitive to the ionic composition of the assay medium. The data are interpreted to support the existence of a general pyridine nucleotide-binding site at the active site of the enzyme and separate from the binding site for oxidized glutathione.