微生物驱动硝酸盐还原耦合亚铁氧化成矿过程的锌胁迫

【目的】探究中性厌氧条件下,金属锌影响下硝酸盐依赖型铁氧化菌Pseudomonas stutzeri LS-2驱动的硝酸盐还原耦合亚铁氧化成矿过程机制,对深入理解中性厌氧环境中微生物亚铁氧化驱动的反硝化作用及重金属固定机制具有重要意义。【方法】以不同Zn(Ⅱ)浓度构建LS-2驱动的亚铁氧化成矿体系,分析不同体系中亚铁氧化速率、硝酸盐还原速率以及形成矿物的结构变化规律。【结果】LS-2驱动的硝酸盐还原耦合亚铁氧化成矿过程中,共存Zn(Ⅱ)降低该过程中硝酸盐的还原速率和亚铁氧化速率。同时,随着Zn(Ⅱ)浓度提高,抑制作用增强。微生物亚铁氧化形成的矿物通过吸附、共沉淀和离子置换等过程固定Zn(Ⅱ),降低Zn(Ⅱ)活性。Zn(Ⅱ)浓度对形成的矿物结构有较大的影响:低浓度Zn(Ⅱ)体系中,形成的矿物为纤铁矿;随着Zn(Ⅱ)浓度的提高,矿物结构与结晶度都有一定程度的变化,当Zn(Ⅱ)达到4 mmol/L时,形成的矿物主要为铁锌尖晶石。【结论】明确了重金属锌对LS-2菌株反硝化及亚铁氧化过程的抑制规律,同时阐明了Zn(Ⅱ)浓度对形成矿物结构的影响。研究结果有助于深入认识中性厌氧环境中重金属与微生物驱动的铁循环和反硝化过程的耦合作用,为土壤重金属污染防治提供理论支撑。     

湖泊微生物反硝化过程及速率研究进展

湖泊中微生物介导的反硝化过程对于区域乃至全球的气候环境变化有着深远的影响。因此,研究湖泊微生物反硝化过程及速率有助于我们深刻理解湖泊氮元素生物地球化学循环规律,全面认识湖泊生境对全球氮循环的贡献。本文综述了湖泊生境中反硝化过程(包括典型的反硝化过程及与其他物质循环耦合的反硝化过程,如与有机氮耦合的共反硝化作用、与碳循环耦合的硝酸盐/亚硝酸盐依赖型厌氧甲烷氧化、与铁循环耦合的硝酸盐依赖型铁氧化、与硫循环耦合的硝酸盐还原硫氧化)的速率、驱动微生物及其影响因素。最后对湖泊反硝化过程研究现状和未来发展方向提出总结与展望。     

双阳极室甲烷微生物燃料电池同步脱氮除硫性能及微生物群落分析

【背景】甲烷厌氧氧化(anaerobic oxidation of methane, AOM)包含反硝化型甲烷厌氧氧化和硫酸盐还原型甲烷厌氧氧化。目前,人们向水体中排放过量的含氮及含硫污染物,引起了严重的环境污染和生态破坏。【目的】利用甲烷厌氧氧化微生物燃料电池(microbial fuel cell, MFC)研究同步脱氮除硫耦合反应机理及反应过程中微生物的多样性信息。【方法】构建了3个微生物燃料电池(N-S-MFC、N-MFC、S-MFC),以甲烷作为唯一碳源,探究其同步脱氮除硫性能,并采用16S rRNA基因高通量测序技术对微生物群落结构进行分析。【结果】N-S-MFC中硝酸盐和硫酸盐的去除率分别为90.91%和18.46%。阳极室中微生物的相对丰度提高,与反硝化及硫酸盐还原菌相关的微生物大量富集,如门水平上拟杆菌门(Bacteroidota)、厚壁菌门(Firmicutes)和脱硫杆菌门(Desulfobacterota),同时属水平上Methylobacterium＿Methylorubrum、Methylocaldum、Methylomonas等常见的甲烷氧化菌增多。【结论...     

利用硝酸盐和亚硝酸盐同步富集厌氧甲烷氧化微生物的比较实验

【背景】反硝化厌氧甲烷氧化(Denitrifying anaerobic methane oxidation,DAMO)是以硝酸盐或亚硝酸盐为电子受体以甲烷为电子供体的厌氧氧化过程,对认识全球碳氮循环、削减温室气体排放和开发废水脱氮新技术等方面具有重要意义。【目的】认识以硝酸盐和亚硝酸盐为电子受体的DAMO微生物富集过程和结果的差异性。【方法】在序批式反应器(Sequencing batch reaetor,SBR)内接种混合物,分别以硝酸盐和亚硝酸盐为电子受体连续培养800 d,定期检测反应器基质浓度变化、计算转化速率;利用16S rRNA基因系统发育分析研究功能微生物的多样性,利用实时荧光定量PCR技术定量测定功能微生物。【结果】以亚硝酸盐为电子受体的1、3号反应器富集到了DAMO细菌,未检测到DAMO古菌;以硝酸盐为电子受体的2号反应器富集到了DAMO细菌和古菌的混合物;3个反应器的脱氮速率经过初始低速期、快速提升期,最终达到稳定,但2号快速提升期开始时间比1、3号晚了80 d左右,达到稳定的时间更长,稳定最大速率为1、3号的44.7%、40.3%。【结论】硝酸盐和亚硝酸盐对富集产物有决定性影响;以硝酸盐为电子受体富集得到的DAMO古菌和细菌协同体系可以长期稳定共存,DAMO古菌可能是协同体系中脱氮速率的限制性因素。     

好氧甲烷氧化耦合反硝化极限脱氮系统的效能及应用

【目的】探究甲烷浓度、温度和氮浓度对好氧甲烷氧化耦合反硝化(AME-D)极限脱氮系统的影响,分析该系统微生物群落结构,并对贵阳某污水处理厂尾水进行应用研究。【方法】采用阶段性实验研究甲烷浓度、温度和氮浓度对系统脱氮效能的影响,通过16SrRNA基因测序技术分析系统中微生物群落结构,利用共焦显微拉曼光谱仪分析实际废水水质变化特征。【结果】甲烷进气比为3%、温度为30°C、氮浓度为20 mg/L时脱氮效果最好,系统的总氮、氨氮和硝酸盐氮平均去除率分别为93.66%、96.13%和92.25%;系统中的主要甲烷氧化菌分别为Methylosarcina(1.84%)、Methylovulum(0.01%)和Crenothrix(0.14%),以及兼性甲烷氧化菌属Methylocystis(1.9%),主要的亚硝化菌为Nitrosomonas(0.008%),硝化菌为Nitrospira (0.42%),反硝化菌为Hyphomicrobium (1.19%)和Pseudomonas (0.61%);采用该系统处理贵阳某污水处理厂尾水时,出水总氮平均浓度达到0.96mg/L,能达到极限脱氮的目的,拉曼光谱分析显示系统对硝酸盐氮和亚硝酸盐氮有较高的去除,甲烷被氧化形成的中间产物可能为醇类或醛类物质,为反硝化菌提供所需碳源。【结论】AME-D极限脱氮由多种微生物协同实现,其功能微生物为甲烷氧化菌、亚硝化菌、硝化菌和反硝化菌,应用研究显示该系统在城镇污水处理系统中具有较大的应用潜力。     

Pseudomonas alcaliphila AD-28的脱氮性能及其关键酶活性

【背景】异养硝化-好氧反硝化菌由于能够同时实现硝化反硝化作用而备受关注,但由于菌的种类不同,其脱氮途径不尽相同,研究菌株脱氮关键酶的种类及其活性可以推测菌株的脱氮途径,从而为菌株在生产上的应用提供技术支撑。【目的】研究Pseudomonas alcaliphila AD-28的脱氮性能及其关键酶的活性,为菌株脱氮分子机理研究奠定基础。【方法】以柠檬酸钠为碳源,以硫酸铵、亚硝酸钠、硝酸钾为氮源,研究菌株AD-28的脱氮性能并检测其关键酶氨单加氧酶(AMO)、羟胺氧化还原酶(HAO)、亚硝酸盐还原酶(NIR)、硝酸盐还原酶(NAR)的酶活性。【结果】菌株AD-28培养24h的菌密度(OD600)可达1.971,对初始浓度为18.85mg/L的氨氮、26.13mg/L的硝酸盐氮、19.47mg/L的亚硝酸盐氮、66.11 mg/L的总氮去除率均达到96%以上;关键酶AMO、HAO、NIR和NAR的比活力分别为0.028、0.003、0.011、0.027 U/mg。【结论】Pseudomonas alcaliphila AD-28能同时进行异养硝化-好养反硝化作用,该菌在AMO作用下将NH4+-N氧化为羟胺,然后由HAO氧化为NO2--N,NO2--N和NO3--N在NIR、NAR等酶的催化作用下脱氮。     

铁矿物强化厌氧氨氧化效能及其微生物机制研究进展

自然界中的氮循环与铁循环相互交联,参与氮循环的厌氧氨氧化（anaerobic ammonium oxidation,anammox）菌的生长代谢及活性发挥也与铁元素紧密关联。自然界广泛存在的铁矿物因具有运行成本低廉、稳定性好、二次污染小等优势,在污水处理领域得到广泛应用。在厌氧氨氧化脱氮系统中引入适量铁矿物,不仅有助于促进anammox菌和铁还原菌的富集,提高功能基因丰度和相关酶活性,还可能通过影响污泥浓度、血红素c含量、胞外聚合物含量和颗粒化程度,改善污泥性能和提高厌氧氨氧化系统的稳定性。同时,铁矿物具有促进体系多种氮素转化途径（如anammox、铁自养反硝化、铁氨氧化、异化硝酸盐还原成铵和反硝化）相耦合的潜能,可以提高anammox污水处理系统的总氮去除率。本文基于铁矿物在促进污水生物脱氮方面的良好性能及其在anammox系统中的变化,从脱氮效能、污泥特性、微生物特征及酶活性等方面,系统综述了铁矿物对厌氧氨氧化系统的强化作用机制,并从anammox菌对铁矿物的利用及铁元素的摄取角度展望了后续的研究方向,以期为铁矿物强化厌氧氨氧化系统的实际应用提供理论和技术指导。     

微生物厌氧甲烷氧化反硝化研究进展

厌氧甲烷氧化反硝化过程(Denitrifying anaerobic methane oxidation,DAMO)以甲烷为电子供体进行反硝化作用,在实现废水脱氮处理的同时,可有效削减温室气体甲烷的排放,从而减缓全球温室效应。相关机制研究集中在逆向产甲烷途径耦合反硝化和亚硝酸盐依赖型厌氧甲烷氧化(nitrite-dependent anaerobic methane oxidation,n-damo)两个方面。鉴于厌氧甲烷氧化反硝化过程对全球碳氮物质循环的重要意义,本文对近年来厌氧甲烷氧化反硝化过程的研究进展进行了概述,着重阐述了有关厌氧甲烷氧化反硝化微生物富集培养物,特别是含Candidatus Methylomirabilis oxyfera(M.oxyfera)富集培养物的微生物特性、甲烷氧化反硝化的机理以及影响因子。在此基础上,探讨了厌氧甲烷氧化反硝化过程未来的研究方向和工业化应用前景。     

一株耐盐的卓贝儿氏菌(Zobellella sp.)的分离鉴定及其硝酸盐还原能力

【背景】好氧反硝化是指在有氧条件下进行反硝化作用,使得硝化和反硝化过程能够在同一反应器中同时发生,是废水脱氮最具竞争力的技术。红树林湿地中蕴藏着丰富的微生物资源,分布着大量好氧反硝化微生物。【目的】了解耐盐微生物的脱氮机制,为含盐废水生物脱氮的工程实践提供理论依据,对一株分离于红树林湿地中的耐盐好氧细菌A63的硝酸盐异化还原能力进行分析。【方法】利用形态学特征及16S rRNA基因序列测定分析,对其种属进行了鉴定,采用单因子实验测定该菌在不同环境因子下的硝酸盐还原能力,并对其反硝化脱氮条件进行了优化。【结果】初步判定该菌株为卓贝儿氏菌(Zobellellasp.),其能在盐度0%-10%、pH5.0-10.0、温度20-40°C范围内进行反硝化脱氮和硝酸盐异化还原为氨(dissimilatorynitratereductiontoammonium,DNRA)作用。菌株A63最适生长碳源为柠檬酸钠(1.2 g/L),适宜脱氮盐度为3%、pH 7.0-7.5、温度30-35°C,且C/N为10。在最适脱氮条件下,该菌株12h内能将培养基中208.8mg/L硝态氮降至0,且仅有少量铵态氮生成...     

反硝化型甲烷厌氧氧化的研究进展

反硝化型甲烷厌氧氧化(denitrifying anaerobic methane oxidation,DAMO)即甲烷厌氧氧化耦合反硝化,是指在厌氧条件下以甲烷作为电子供体,NO2-/NO3-作为电子受体的反硝化过程。甲烷是一种温室气体,其引起的温室效应是等物质量CO2的20~30倍。DAMO过程利用甲烷代替常规碳源进行脱氮,有利于减少温室效应,并改善氮循环。研究发现,Candidatus Methylomirabilis oxyfera细菌和Candidatus Methanoperedens nitroreducens古菌是参与DAMO过程的2类主要功能微生物,前者通过内部好氧机制耦合亚硝酸盐还原与甲烷的厌氧氧化,后者则通过逆向产甲烷途径耦合硝酸盐还原与甲烷的厌氧氧化。本文详细阐述了M.oxyfera细菌和M.nitroreducens古菌细胞内代谢途径,着重总结了甲烷、NO2-/NO3-、反应器构型、温度等因素对DAMO性能的影响。并对DAMO实际应用方面的研究现状做了调研。在DAMO功能微生物作用机制、快速富集及影响因素的进一步深入研究的基础上,推进DAMO污水脱氮工艺的应用是未来的主要研究热点和发展方向。     

Abiotic oxidation of Fe(II) by reactive nitrogen species in cultures of the nitrate‐reducing Fe(II) oxidizer Acidovorax sp. BoFeN1 – questioning the existence of enzymatic Fe(II) oxidation

Nitrate‐reducing, Fe(II)‐oxidizing bacteria were suggested to couple with enzymatic Fe(II) oxidation to nitrate reduction. Denitrification proceeds via intermediates (, NO) that can oxidize Fe(II) abiotically at neutral and particularly at acidic pH. Here, we present a revised Fe(II) quantification protocol preventing artifacts during acidic Fe extraction and evaluate the contribution of abiotic vs. enzymatic Fe(II) oxidation in cultures of the nitrate‐reducing, Fe(II) oxidizer Acidovorax sp. BoFeN1. Sulfamic acid used instead of HCl reacts with nitrite and prevents abiotic Fe(II) oxidation during Fe extraction. Abiotic experiments without sulfamic acid showed that acidification of oxic Fe(II) nitrite samples leads to 5.6‐fold more Fe(II) oxidation than in anoxic samples because the formed NO becomes rapidly reoxidized by O₂, therefore leading to abiotic oxidation and underestimation of Fe(II). With our revised protocol using sulfamic acid, we quantified oxidation of approximately 7 mm of Fe(II) by BoFeN1 within 4 days. Without addition of sulfamic acid, the same oxidation was detected within only 2 days. Additionally, abiotic incubation of Fe(II) with nitrite in the presence of goethite as surface catalyst led to similar abiotic Fe(II) oxidation rates as observed in growing BoFeN1 cultures. BoFeN1 growth was observed on acetate with N₂O as electron acceptor. When adding Fe(II), no Fe(II) oxidation was observed, suggesting that the absence of reactive N intermediates (, NO) precludes Fe(II) oxidation. The addition of ferrihydrite [Fe(OH)₃] to acetate/nitrate BoFeN1 cultures led to growth stimulation equivalent to previously described effects on growth by adding Fe(II). This suggests that elevated iron concentrations might provide a nutritional effect rather than energy‐yielding Fe(II) oxidation. Our findings therefore suggest that although enzymatic Fe(II) oxidation by denitrifiers cannot be fully ruled out, its contribution to the observed Fe(II) oxidation in microbial cultures is probably lower than previously suggested and has to be questioned in general until the enzymatic machinery‐mediating Fe(II) oxidation is identified.     

Oxidation of Fe(II)‐EDTA by nitrite and by two nitrate‐reducing Fe(II)‐oxidizing Acidovorax strains

The enzymatic oxidation of Fe(II) by nitrate‐reducing bacteria was first suggested about two decades ago. It has since been found that most strains are mixotrophic and need an additional organic co‐substrate for complete and prolonged Fe(II) oxidation. Research during the last few years has tried to determine to what extent the observed Fe(II) oxidation is driven enzymatically, or abiotically by nitrite produced during heterotrophic denitrification. A recent study reported that nitrite was not able to oxidize Fe(II)‐EDTA abiotically, but the addition of the mixotrophic nitrate‐reducing Fe(II)‐oxidizer, Acidovorax sp. strain 2AN, led to Fe(II) oxidation (Chakraborty & Picardal, 2013). This, along with other results of that study, was used to argue that Fe(II) oxidation in strain 2AN was enzymatically catalyzed. However, the absence of abiotic Fe(II)‐EDTA oxidation by nitrite reported in that study contrasts with previously published data. We have repeated the abiotic and biotic experiments and observed rapid abiotic oxidation of Fe(II)‐EDTA by nitrite, resulting in the formation of Fe(III)‐EDTA and the green Fe(II)‐EDTA‐NO complex. Additionally, we found that cultivating the Acidovorax strains BoFeN1 and 2AN with 10 mm nitrate, 5 mm acetate, and approximately 10 mm Fe(II)‐EDTA resulted only in incomplete Fe(II)‐EDTA oxidation of 47–71%. Cultures of strain BoFeN1 turned green (due to the presence of Fe(II)‐EDTA‐NO) and the green color persisted over the course of the experiments, whereas strain 2AN was able to further oxidize the Fe(II)‐EDTA‐NO complex. Our work shows that the two used Acidovorax strains behave very differently in their ability to deal with toxic effects of Fe‐EDTA species and the further reduction of the Fe(II)‐EDTA‐NO nitrosyl complex. Although the enzymatic oxidation of Fe(II) cannot be ruled out, this study underlines the importance of nitrite in nitrate‐reducing Fe(II)‐ and Fe(II)‐EDTA‐oxidizing cultures and demonstrates that Fe(II)‐EDTA cannot be used to demonstrate unequivocally the enzymatic oxidation of Fe(II) by mixotrophic Fe(II)‐oxidizers.     

Potential Role of Nitrite for Abiotic Fe(II) Oxidation and Cell Encrustation during Nitrate Reduction by Denitrifying Bacteria

Microorganisms have been observed to oxidize Fe(II) at neutral pH under anoxic and microoxic conditions. While most of the mixotrophic nitrate-reducing Fe(II)-oxidizing bacteria become encrusted with Fe(III)-rich minerals, photoautotrophic and microaerophilic Fe(II) oxidizers avoid cell encrustation. The Fe(II) oxidation mechanisms and the reasons for encrustation remain largely unresolved. Here we used cultivation-based methods and electron microscopy to compare two previously described nitrate-reducing Fe(II) oxidizers ( Acidovorax sp. strain BoFeN1 and Pseudogulbenkiania sp. strain 2002) and two heterotrophic nitrate reducers (Paracoccus denitrificans ATCC 19367 and P. denitrificans Pd 1222). All four strains oxidized ∼8 mM Fe(II) within 5 days in the presence of 5 mM acetate and accumulated nitrite (maximum concentrations of 0.8 to 1.0 mM) in the culture media. Iron(III) minerals, mainly goethite, formed and precipitated extracellularly in close proximity to the cell surface. Interestingly, mineral formation was also observed within the periplasm and cytoplasm; intracellular mineralization is expected to be physiologically disadvantageous, yet acetate consumption continued to be observed even at an advanced stage of Fe(II) oxidation. Extracellular polymeric substances (EPS) were detected by lectin staining with fluorescence microscopy, particularly in the presence of Fe(II), suggesting that EPS production is a response to Fe(II) toxicity or a strategy to decrease encrustation. Based on the data presented here, we propose a nitrite-driven, indirect mechanism of cell encrustation whereby nitrite forms during heterotrophic denitrification and abiotically oxidizes Fe(II). This work adds to the known assemblage of Fe(II)-oxidizing bacteria in nature and complicates our ability to delineate microbial Fe(II) oxidation in ancient microbes preserved as fossils in the geological record.     

Effect of Reduced Sulfur Species on Chemolithoautotrophic Pyrite Oxidation with Nitrate

We compared the response at neutral pH of some denitrifiers to different electron donors such as reduced sulfur (pyrite, S(0), and marcasite) and reduced Fe. Chemolithoautotrophic oxidation of pyrite with nitrate as electron acceptor was not possible when the pyrite was in a pure crystalline form, whereas oxidation of synthesized FeS₂ of low crystallinity and of S(0) with nitrate as electron acceptor was possible. Neither nitrite nor sulfate was formed when Fe(II)-oxidizing strain Acidovorax sp. BoFeN1 was tested. Microbial reduction of nitrate appears to be induced via S oxidation but not via Fe oxidation.     

过表达亚硝酸盐还原酶的重组大肠杆菌辅助污水短程硝化

【目的】为了体现并突出亚硝酸盐还原酶在污水脱氮以及短程硝化中的重要性,对过表达亚硝酸盐还原酶的大肠杆菌进行了污水脱氮的研究。【方法】通过转化带有亚硝酸盐还原酶基因的重组质粒,将亚硝酸盐还原酶在大肠杆菌中过表达,通过分析重组大肠杆菌的产物研究了该酶的表达及还原亚硝酸盐的情况,通过将该重组菌与已报道的硝化-反硝化细菌或生活污水进行混合培养,研究重组菌用于辅助氨氮去除的短程硝化能力。【结果】重组大肠杆菌能正确表达亚硝酸盐还原酶,OD600=2.0的菌悬液在2 h内还原约1 mmol/L的亚硝酸盐,并产生几乎等量的一氧化氮;重组大肠杆菌与Acinetobacter sp.YF14菌株等比例混合时,12 h能够提高氨氮脱氮效率约(36.0±7.4)%,且在4 h时,最大亚硝酸盐的积累量减少37%;重组大肠杆菌(OD600=1.0)12 h内能够提高污水厂活性污泥的脱氮效率约(31.0±5.7)%,且未检测到亚硝酸盐和硝酸盐的积累;溶氧水平对于亚硝酸盐还原酶重组菌辅助脱氮具有明显的影响,中等溶氧量[(6.4?0.7)mg/L]时脱氮效果最好。【结论】过表达亚硝酸盐还原酶的大肠杆菌可以提高污水脱氮的短程硝化能力。     

Fe(III) mineral formation and cell encrustation by the nitrate-dependent Fe(II)-oxidizer strain BoFeN1

Understanding the mechanisms of anaerobic microbial iron cycling is necessary for a full appreciation of present‐day biogeochemical cycling of iron and carbon and for drawing conclusions about these cycles on the ancient Earth. Towards that end, we isolated and characterized an anaerobic nitrate‐dependent Fe(II)‐oxidizing bacterium from a freshwater sediment. The 16SrRNA gene sequence of the isolated bacterium (strain BoFeN1) places it within the β‐Proteobacteria, with Acidovorax sp. strain G8B1 as the closest known relative. During mixotrophic growth with acetate plus Fe(II) and nitrate as electron acceptor, strain BoFeN1 forms Fe(III) mineral crusts around the cells. The amount of the organic cosubstrate acetate present seems to control the rate and extent of Fe(II) oxidation and the viability of the cells. The crystallinity of the mineral products is influenced by nucleation by Fe minerals that are already present in the inoculum.     

天然Fe(Ⅱ)矿物-生物质强化微生物还原固定五价钒研究

【目的】重金属钒的环境危害日益受到关注,微生物可实现高毒性的五价钒[pentavalent vanadium, V(Ⅴ)]的还原固定,其中电子供体是微生物还原V(Ⅴ)的关键,尽管天然Fe(Ⅱ)矿物和天然生物质均被报道可单独支持微生物还原V(Ⅴ),而基于两者构建的混养体系中微生物还原V(Ⅴ)的特征尚未揭示。【方法】本研究对天然Fe(Ⅱ)矿物和生物质进行优选并复配组合,探究混养生物体系中五价钒[V(Ⅴ)]的还原机理。【结果】磁黄铁矿和木屑对V(Ⅴ)的去除效率最高,分别为54.2%±3.4%和67.1%±3.1%。当优选的磁黄铁矿与木屑组合复配比例为1:3时可达到最高的V(Ⅴ)去除效率82.7%±3.1%。V(Ⅴ)被还原为不溶性V(Ⅳ)沉淀,Fe(Ⅱ)和S(–Ⅱ)分别被氧化为Fe(Ⅲ)和SO₄^2-。在混养体系中,脱硫菌(Desulfurivibrio)和硫菌属(Thiobacillus)等自养菌属可能参与磁黄铁矿的氧化与V(Ⅴ)还原,并利用无机碳源合成有机中间代谢产物,与无胆甾原体属(Acholeplasma)等纤维素降解菌分解木屑的产物一起,被B...     

Ecophysiology and the energetic benefit of mixotrophic Fe(II) oxidation by various strains of nitrate-reducing bacteria

In order to assess the importance of nitrate-dependent Fe(II) oxidation and its impact on the growth physiology of dominant Fe oxidizers, we counted these bacteria in freshwater lake sediments and studied their growth physiology. Most probable number counts of nitrate-reducing Fe(II)-oxidizing bacteria in the sediment of Lake Constance, a freshwater lake in Southern Germany, yielded about 10⁵ cells mL⁻¹ of the total heterotrophic nitrate-reducing bacteria, with about 1% (10³ cells mL⁻¹) of nitrate-reducing Fe(II) oxidizers. We investigated the growth physiology of Acidovorax sp. strain BoFeN1, a dominant nitrate-reducing mixotrophic Fe(II) oxidizer isolated from this sediment. Strain BoFeN1 uses several organic compounds (but no sugars) as substrates for nitrate reduction. It also reduces nitrite, dinitrogen monoxide, and O₂, but cannot reduce Fe(III). Growth experiments with cultures amended either with acetate plus Fe(II) or with acetate alone demonstrated that the simultaneous oxidation of Fe(II) and acetate enhanced growth yields with acetate alone (12.5 g dry mass mol⁻¹ acetate) by about 1.4 g dry mass mol⁻¹ Fe(II). Also, pure cultures of Pseudomonas stutzeri and Paracoccus denitrificans strains can oxidize Fe(II) with nitrate, whereas Pseudomonas fluorescens and Thiobacillus denitrificans strains did not. Our study demonstrates that nitrate-dependent Fe(II) oxidation contributes to the energy metabolism of these bacteria, and that nitrate-dependent Fe(II) oxidation can essentially contribute to anaerobic iron cycling.