沙芥幼苗叶片解剖结构和光合作用对干旱胁迫的响应

为了了解干旱胁迫对植物光合作用和叶片结构的影响,明确植物光合作用和结构对干旱胁迫的响应,本研究以沙生植物、中国特有种---沙芥为材料,采用Li-6400光合仪和常规石蜡切片法,研究了干旱胁迫下沙芥光合参数、叶片解剖结构的变化,结合前期对沙芥叶片内活性氧物质含量变化的研究,试图阐述沙芥叶片应对干旱胁迫的机制,揭示沙生植物—沙芥在干旱环境中的生存策略,为植物耐旱性提供理论依据。结果表明：随着土壤含水量下降,净光合速率(Pn)、蒸腾速率(Tr)、气孔导度(Gs)、叶片厚度、上表皮厚度、下表皮厚度呈下降趋势;海绵组织厚度呈先下降后上升的趋势;胞间二氧化碳浓度(Ci)呈上升的趋势;气孔限制值(Ls)、水分利用率(WUE)、栅栏组织和栅栏组织/海绵组织和叶片组织结构紧密度(CTR)呈先先上升后下降的趋势;且在土壤含水量大于39% WHC时沙芥光合和结构受影响较小,在土壤含水量低于39% WHC时,沙芥光合作用受到抑制,而叶片紧密度变大,能够较好的抵御干旱环境。结果表明干旱胁迫下沙芥幼苗叶片光合作用的下降是非气孔因素造成的,且其叶片结构的变化会影响光合作用,光合作用通过产生活性氧对结构也有影响。说明沙芥能够很好的适应中度干旱以上的环境,在重度干旱环境中沙芥通过调节叶片结构以适应环境,这可能是沙芥能够在沙漠地区生存繁殖的原因之一。     

乙草胺对蛋白核小球藻的毒性效应研究

乙草胺是我国使用量最大的除草剂之一,在水体中广泛存在。已有研究证明,乙草胺对人类、老鼠和鱼类具有毒害效应,而关于其对浮游植物影响的研究较少。以蛋白核小球藻(Chlorella pyrenoidosa)为模型,使用1～10 000μg·L~(-1)的乙草胺对其进行7 d的暴露实验,考察小球藻生长性能、叶绿素含量、光合作用产氧量以及光合作用相关基因(pbsA、rbcL和rbcS)表达的变化。结果表明,较低浓度的乙草胺可刺激蛋白核小球藻生长,而较高浓度乙草胺则会抑制其生长;并且乙草胺会通过影响小球藻叶绿素的含量而影响光合作用产氧量;小球藻光合作用相关基因pbsA、rbcL和rbcS表达大多显著上升,这可能是对乙草胺胁迫响应的反馈调节。研究表明,乙草胺会对蛋白核小球藻的生长及光合作用产生影响。     

干旱胁迫对香樟幼树生长及光合特性的影响

通过盆栽和持续干旱研究了干旱胁迫(以2 d为一个处理间隔,持续干旱0-16 d)对香樟(Cinnamomum camphora)幼树生长及光合特性的影响.结果显示:(1)干旱胁迫下香樟幼树的地径、树高生长量受到了抑制.轻度、中度干旱处理(干旱时间2-8 d)叶片含水量和叶片相对含水量与对照差异均不显著,重度干旱处理(干旱时间10 d)下显著低于对照(P0.01);(2)干旱胁迫影响了香樟叶片光合作用的日变化进程,妨碍了其有机物质积累;(3)干旱胁迫下香樟叶片光合色素总量先升高后降低,在干旱第8天达到最高.所有干旱处理的净光合速率(Pn)、蒸腾速率(Tr)、气孔导度(Gs)均受到不同程度的抑制.气孔因素和非气孔因素共同作用影响香樟幼树的光合作用,在干旱初期(干旱时间2-8 d)气孔因素起主导作用,干旱后期(干旱时间10 d)非气孔因素起主导作用;(4)干旱胁迫下香樟幼树叶片的表观量子效率(AQY)、RuBP羧化速率(CE)、光补偿点(LCP)、光饱和点(LSP)及CO2补偿点(CCP)均显著降低,表明干旱会降低香樟幼树对环境中光照和CO2的利用及适应能力.综上,干旱胁迫下香樟幼树的水分生理状况变差,光合能力及光合日变化进程受到影响,对环境中光照和CO2的利用及适应能力也明显降低,最终香樟幼树的形态生长受到抑制.图3表3参35     

高等植物对甲醇的释放和利用

植物可向大气中释放一种挥发性的有机气体——甲醇,同时对这种气体可加以利用。在详细阐述甲醇的产生、释放和可能的代谢机制的基础上,通过不同浓度的甲醇溶液喷施牡丹叶片,测定其对光合作用过程及叶绿素荧光参数变化的影响。结果表明,光合作用有较大改善:光合速率明显提高,气孔导度增加,叶内CO2浓度也有一定幅度改善。叶绿素荧光参数(qN和NPQ)以及电子传递速率(ETR)发生较大改变;Fm/Fo,Fv/Fo和ΦPSII的下降可能与甲醇对牡丹叶片的双向效应(促进性和毒性)有关,这取决于喷施的浓度、次数和时间。初步的结果显示:甲醇提高光合作用速率的同时,并没有伴随光合效率和机能的改善和提高。期间的气孔导度和胞内CO2浓度的提高以及非辐射能耗散(qN和NPQ)和光呼吸的降低可能是牡丹叶片光合作用速率提高的主要原因。     

PVC塑料浸出液对3种海洋微藻光合作用及生长的影响

海洋微塑料作为一类新型环境污染物已经成为全球性环境问题。运用水样叶绿素荧光仪(Water-PAM)研究了不同浓度软聚氯乙烯(polyvinyl chloride, PVC)和硬PVC浸出液(0、50、100和200 g·L~(-1))胁迫下球等鞭金藻(Isochrysis galbana)、中肋骨条藻(Skeletonema costatum)和小球藻(Chlorella sp.)3种海洋微藻叶绿素荧光特性,包括PSⅡ最大量子产量(F_v/F_m)、PSⅡ实际量子产量(Yield)、光化学淬灭(qP)和PSⅡ最大相对电子传递速率(rETR_(max))的变化,同时检测微藻的生长状况。结果表明,球等鞭金藻(金藻门)和中肋骨条藻(硅藻门)的4项光合作用参数在软PVC浸出液胁迫的96 h内均显著下降,且随软PVC浸出液浓度增加,下降幅度增大,在实验后期(48～96 h)达到最小值,表现为抑制作用。96 h时,球等鞭金藻和中肋骨条藻的细胞密度均在软PVC浸出液200 g·L~(-1)处理组达到最小值,分别占对照组的3.20%和11.90%。硬PVC浸出液胁迫对球等鞭金藻和中肋骨条藻的4项光合作用参数具有显著影响(P<0.05),球等鞭金藻的4项参数均显著高于对照组。中肋骨条藻的相关光合作用参数均显著低于对照组。72 h时球等鞭金藻和中肋骨条藻的细胞密度分别在硬PVC浸出液100 g·L-1和200 g·L~(-1)处理组达到最小值,为对照组的67.90%和82.50%,表现为抑制作用。小球藻(绿藻门)的各光合作用参数和细胞密度在软PVC和硬PVC浸出液胁迫的96 h内未产生显著变化。该研究证实PVC浸出液对微藻光合系统具有干扰作用,对海洋生态系统具有潜在风险。     

孑遗植物四合木(Tetraena mongolica)迁地保护中的光合作用日变化特征与生理生态适应性

为了进一步廓清迁地保护条件下孑遗植物四合木(Tetraena mongolica)的光合生理生态适应性,在分析了瞬时光合效率的基础上,应用LI-6400光合作用测定系统测定了迁地保护试验区的四合木以及原生境伴生种白刺(Nitraria tangutorum)的光合作用日变化,并测定了其生长量。结果表明:四合木实生苗的生长南北冠幅大小依次为乌海四合木核心区实生苗(26.48cm×27.26 cm)鄂尔多斯实生苗(21.27 cm×21.75 cm)阿拉善实生苗(19.25 cm×18.27 cm)。在原生境地乌海四合木核心区种植的实生苗与阿拉善实生苗之间的生长量存在显著差异(P≤0.01),与鄂尔多斯实生苗之间的生长量存在显著差异(P≤0.05)。迁地保护条件下四合木生实生苗植株叶片光合速率Pn日变化均呈"双峰"曲线。不同试验区四合木光合作用日变化(Pn)、蒸腾速率(Tr)、气孔导度(Gs)和胞间CO2浓度(Ci)均表现出明显的分异。迁地保护四合木条件下原生境地栽培的四合木实生苗的光合速率鄂尔多斯栽培的四合木实生苗的光合速率阿拉善栽培的四合木实生苗。鉴此可以作进一步推论,孑遗濒危植物四合木从原生境地西鄂尔多斯核心区(乌海)东移进行迁地保护具有更高的生理生态适应性和生境适宜性。但完成"从种子到种子"进而实现"保存性和代表性",最终实现四合木迁地保护的"保持性和防止性",保持其遗传多样性和遗传稳定性,最终成功实现四合木的迁地保护仍有待作进一步探索和深入研究。     

河套灌区总排干沟过饱和溶解氧出现因素分析

水中溶解氧(DO)是衡量水质的一个重要参数,是指溶解在水中的分子态氧,它的饱和程度与空气中氧的分压,大气压和水温有密切关系;影响其含量的因素主要有:曝气作用、光合作用、呼吸作用与废弃物的氧化作用.     

除草剂对植物光合作用和吸肥能力影响初探

本文应用P~(32)、C~(14)同位素示踪技术研究棉花与大豆施用三种除草剂对植物吸肥能力和光合作用的影响。结果表明,拿捕净抑制棉花对P~(32)的吸收,稳杀得反而起促进作用,禾草克影响不明显,三种除草剂对光合作用的抑制影响,稳杀得>拿捕净>禾草克。施药一周后,大豆和棉花的光合作用已恢复正常,施用拿捕净和稳杀得的两种作物对P~(32)的吸收均起促进作用,而施用禾草克的作物对P~(32)吸收已逐趋正常。     

不同氮磷水平下中肋骨条藻对营养盐的吸收及光合特性

研究了不同氮、磷水平下中肋骨条藻(Skeletonema costatum)对营养盐的吸收动力学、生长和光合作用特性，结果表明，培养基中氮或磷浓度的改变对中肋骨条藻比生长速率影响不大，各种条件下藻细胞的比生长速率约为1．51—1．60d^-1，其中，藻细胞在低氮条件下的比生长速率略高，为1．60d^-1；低氮和低磷条件下藻细胞稳定期的生物量明显下降，分别比中氮和高氮下减少了27％和41％，而比中磷和高磷减少了64％和65％,低营养源(低氮或低磷)状态下生长的藻细胞具有较低的单位细胞表示的光饱和的光合作用速率(Pm^cell)和光合效率(α^crll)。尽管在低氮或低磷条件下生长的藻细胞单位叶绿素a的含量较低，但具有较高的活性，以单位叶绿素a表示的光饱和的光合作用速率(Pm^chla)和光合效率(α^chla)均与高氮或高磷条件下生长的藻细胞相当，这可能是不同氮、磷水平下比生长速率差异不大的原因．中肋骨条藻细胞对氮和磷吸收的适当比值(N／P)为0．8-2．6．图3表4参17     

黄土塬区旱作果园的复合经营范式

旱作果园中进行间作,尤其苹果产出前的间作,是黄土塬区果业发展中较为普遍的复合经营形式。为强调以果为主以及建立良好的控制性间作制度,通过典型塬区面上间作类型调查及实地对比测定主要作物种植影响下的苹果(Malus pumila)树高、地径、分枝性以及3 m深土壤剖面含水量,分析间作基础及有关间作适宜性,探讨规范化运作模式。结果表明,随果树生长发育,可划分3个不同间作时期(幼龄前期、幼龄后期和成龄期)。从幼龄后期开始对间作物选择趋于严格。浅根性低矮作物具有明显时空优势,西瓜(Citrullus vulgaris)、甘薯(Ipomoea batatas)间作果树生长优于小麦(Triticum aestivum)、玉米(Zea mays)间作。深根性高秆作物[小麦(Triticum aestivum)、玉米(Zea mays)、油菜(Brassica campestris)、谷(Setaria italica)]中,玉米抑制果树生长影响较低,小麦仅以留存树盘间作致使约65%的果树植株不发生分枝。不同间作物之间的耗水性有所差异,其中小麦耗水深度可达3m,玉米1 m,大豆0.4 m,白三叶草(Trifolium repens)1.6 m;小麦及5～9年生白三叶草年内土壤水分消耗得不到补充恢复。浅根性低矮作物地下竞争较弱,但白三叶草竞争不可忽视。生态位分离是间作关键,尤其是深根性高秆作物以及与果树根系重置的浅根性作物。小麦收获后不宜复种及连作,白三叶草衰败时有必要及早翻耕处理。间作需要重视养地作物,综合考虑生态位分离、轮作、适当产量或收益、果树衰败等方面因素。     

共存阴阳离子对针铁矿表面磷固存机制的影响研究

磷素(P)兼具重要养分元素的利和潜在面源污染的弊,其在土壤环境中的固存行为及其迁移转化过程受到广泛关注.该研究选取黄、红壤中典型矿物(针铁矿、赤铁矿及高岭石)为模式矿物,在排除pH干扰的条件下,开展了共存阴(As(V))阳(Cd(II))离子对矿物表面P(V)固存机制的影响研究.结果表明:P(V)在不同矿物表面的吸附效...     

Cu2+、Zn2+和Cd2+对蟾蜍蝌蚪的联合毒性

以蟾蜍蝌蚪为试验材料,采用联合指数相加法,研究了重金属铜(Cu)、锌(Zn)和镉(Cd)离子对蟾蜍蝌蚪的急性毒性和联合毒性效应.结果表明,Cu2 、Zn2 和Cd2 对蟾蜍蝌蚪的毒性顺序为Cu2 >Cd2 >Zn2 ,48 h的半致死浓度LC50分别为0.514、9.224、33.56 mg L-1;96 h的半致死浓度LC50分别为0.288、8.142、30.76 mg L-1.联合毒性试验结果表明,Cu2 与Zn2 及Zn2 与Cd2 共存时的联合毒性为拮抗作用;Cu2 与Cd2 共存时的联合毒性为毒性剧增的协同作用;Cu2 、Zn2 与Cd2 三者联合时的毒性为协同作用.表6参18     

铁(III)-丙酮酸盐配合物光解引发水中铬(Ⅵ)还原

初步研究了含有Fe(III)及丙酮酸盐的溶液在高压汞灯照射下对铬(VI)的光还原反应.考察了溶液pH值、Fe(III)浓度、丙酮酸钠浓度、Cr(VI)浓度对反应的影响.分析了光还原反应的动力学及反应机制.结果表明:铁丙酮酸盐体系能光还原Cr(VI);最佳pH为3.0;Cr(VI)光还原的初始速率随着加入的铁(III)、丙酮酸盐、Cr(VI)初始浓度的增加而增加;实验条件下的表观动力学方程为:-dCCr(VI)/dt=0.021[Cr(VI)]0.39[Fe(III)]1.05[CH3COCOONa]0.39;Fe(III)-丙酮酸盐配合物光解产生的Fe(II)是Cr(VI)的主要还原剂.     

Effects of Cr(III) organic compounds on Lactobacillus plantarum

Biotransformation of Cr(VI) to less toxic Cr(III) has been known to produce insoluble Cr(III) compounds and soluble Cr(III) organic complexes. However, recent research reports have indicated that Cr(III) organic complexes are relatively stable in the environment. Little has been reported on the fate and toxic effects of Cr(III) organic compounds on organisms. In this study, the toxic effects of the soluble Cr(III) organic complexes [Cr(III) citrate, Cr(III) histidine, Cr(III) lactate and Cr(III) glutamate] to a local strain of Lactobacillus plantarum isolated from sauerkraut was investigated. Growth inhibition, viable cell count and lactic acid inhibition were measured to determine the toxicity potential of the test compounds. The EC₅₀ values of Cr(III) citrate, Cr(III) histidine, Cr(III) lactate, and Cr(III) glutamate, calculated from the percent growth inhibition were found to be 56 mg L^?1, 70 mg L^?1, 81 mg L^?1, and 85 mg L^?1, respectively. Similar trend was observed in the viable cell counts and lactic acid production. Cr(VI) was observed to be more toxic than the Cr(III) organic compounds, while inorganic Cr(III) was the least toxic. The severity seemed to increase with increase in chromium compounds’ concentration. The results showed that Cr(III) citrate was the most toxic Cr(III) organic compound, while Cr(III) glutamate was the least.     

耕地土壤铜、镉、锌形态及生物有效性研究

土壤重金属总量常被用来评估土壤质量安全,但是大量事实说明单纯用土壤重金属总量并不能完全说明土壤重金属的生物有效性及其环境风险。相对于国内外常用的Tessier的五态方法,欧共体标准物质局提出的三步提取法(BCR法),中国地质调查局地质连续提取法的七态标准少见报道。本研究选取河南平原耕地样品,采用中国地质调查局地质连续提取法(DD2005-03)进行耕地中重金属元素(Cu、Cd、Zn)的形态分布,结果表明:Cu、Zn主要以残渣态存在,其残渣态分别占全量的55.80%和67.35%。Cd以离子交换态为主,占全量的27.30%。Cu、Cd、Zn各态含量占全量比例的顺序是,Cu:残渣态弱有机结合交换态铁锰氧化态碳酸盐结合态强有机结合态水溶态离子交换态。Cd:离子交换态弱有机结合交换态强有机结合态残渣态碳酸盐结合态铁锰氧化态水溶态。Zn:残渣态铁锰氧化态弱有机盐结合态离子交换态强有机结合态碳酸盐态水溶态。从生物可利用性系数k来看,Cd主要以活动性较大的状态存在,很容易被作物吸收。     

Accumulation and translocation of heavy metals in soil and plants from fly ash contaminated area

The present investigation deals with the accumulation of heavy metals in fields contaminated with fly ash from a thermal power plant and subsequent uptake in different parts of naturally grown plants. Results revealed that in the contaminated site, the mean level of all the metals (Cd, Zn, Cr, Pb, Cu, Ni, Mn and Fe) in soil and different parts (root and shoots) of plant species were found to be significantly (p<0.01) higher than the uncontaminated site. The enrichment factor (EF) of these metals in contaminated soil was found to be in the sequence of Cd (2.33) > Fe (1.88) > Ni (1.58) > Pb (1.42) > Zn (1.31) > Mn (1.27) > Cr (1.11) > Cu (1.10). Whereas, enrichment factor of metals in root and shoot parts, were found to be in the order of Cd (7.56) > Fe (4.75) > Zn (2.79) > Ni (2.22) > Cu (1.69) > Mn (1.53) > Pb (1.31) > Cr (1.02) and Cd (6.06) approximately equal Fe (6.06) > Zn (2.65) > Ni (2.57) > Mn (2.19) > Cu (1.58) > Pb (1.37) > Cr (1.01) respectively. In contaminated site, translocation factor (TF) of metals from root to shoot was found to be in the order of Mn (1.38) > Fe (1.27) > Pb (1.03) > Ni (0.94) > Zn (0.85) > Cd (0.82) > Cr (0.73) and that of the metals Cd with Cr, Cu, Mn, Fe; Cr with Pb, Mn, Fe and Pb with Fe were found to be significantly correlated. The present findings provide us a clue for the selection of plant species, which show natural resistance against toxic metals and are efficient metal accumulators.     

Arsenic and chromate removal from water by iron chips—Effects of anions

The purpose of this study is to estimate the removal efficiency of As and Cr (VI) by one kind of industrial waste — iron chips, as well as to estimate the effects of typical inorganic anions (sulfate, phosphate, and nitrate), and typical organic anions (citrate, oxalate, and humate) on As or Cr (VI) removal. The results showed that 98% of As (V) and 92% of As (III) could be removed from aqueous phase by the iron chips within 60 min. Compared with As species, Cr (VI) was removed much more rapidly and efficiently with 97% of Cr (VI) being removed within 25 min. The removal efficiency for arsenic was in the order: As (III) (sulfate), As (III) (nitrate) or As (III), As (III) (humate), As (III) (oxalate), As (III) (citrate), As (III) (phosphate), and for chromate was in the order: Cr (VI) (sulfate), Cr (VI) (phosphate) or Cr (VI) (nitrate) or Cr (VI) (oxalate), Cr (VI), Cr (VI) (citrate), Cr (VI) (humate). In all the treatments, pH level increased with time except for As (III), the removal of which was either without anions or in the presence of humate or nitrate.     

应用物种敏感性分布评估中国近海和福建主要海湾水体重金属生态风险

利用物种敏感性分布(species sensitivity distribution,SSD)方法构建常见重金属元素对海洋生物的SSD曲线,在此基础上,结合实际调查数据,计算了中国近海7种重金属(As、Cd、Cr、Cu、Hg、Pb、Zn)和福建主要海湾6种重金属(As、Cd、Cu、Hg、Pb、Zn)对海洋生物的潜在影响比例(PAF),并分析了各种重金属在相应海区的联合生态风险(msPAF)。结果表明,中国近海水体重金属对海洋生物的生态风险大小顺序为:渤海(20.67%)>黄海(18.39%)>东海(15.94%)>南海(11.26%)。福建主要海湾水体重金属对海洋生物的生态风险大小顺序为:泉州湾(47.44%)>厦门湾(47.16%)>罗源湾(43.03%)>沙埕港(34.65%)>深沪湾(30.34%)>三沙湾(28.64%)>闽江口(20.55%)>诏安湾(20.42%)>兴化湾(18.37%)>湄洲湾(17.24%)。     

Co-present Pb(II) accelerates the oxidation of organic contaminants by permanganate: Role of Pb(III)

• Simultaneous removal of organic contaminants and Pb(II) was achieved by Mn(VII). • Pb(II) enhanced Mn(VII) oxidation performance over a wide pH range. • Pb(II) did not alter the pH-rate profile for contaminants oxidation by Mn(VII). • Mn(VII) alone cannot oxidize Pb(II) effectively at pH below 5.0. • Pb(III) plays important roles on enhancing Mn(VII) decontamination process. The permanganate (Mn(VII)) oxidation has emerged as a promising technology for the remediation and treatment of the groundwater and surface water contaminated with the organic compounds. Nonetheless, only a few studies have been conducted to explore the role of the heavy metals (especially the redox-active ones) during the Mn(VII) oxidation process. In this study, taking Pb(II) as an example, its influence on the Mn(VII) decontamination performance has been extensively investigated. It was found that, with the presence of Pb(II), Mn(VII) could degrade diclofenac (DCF), 2,4-dichlorophenol, and aniline more effectively than without. For instance, over a wide pH range of 4.5–8.0, the dosing of 10 μmol/L Pb(II) accelerated the DCF removal rate from 0.006–0.25 min⁻¹ to 0.05–0.46 min⁻¹ with a promotion factor of 1.9–9.4. Although the UV-vis spectroscopic and high resolution transmission electron microscopy analyses suggested that Mn(VII) could react with Pb(II) to produce Mn(IV) and Pb(IV) at pH 6.0–8.0, further experiments revealed that Pb(II) did not exert its enhancing effect through promoting the generation of MnO₂, as the reactivity of MnO₂ was poor under the employed pH range. At pH below 5.0, it was interesting to find that, a negligible amount of MnO₂ was formed in the Mn(VII)/Pb(II) system in the absence of contaminants, while once MnO₂ was generated in the presence of contaminants, it could catalyze the Pb(II) oxidation to Pb(IV) by Mn(VII). Collectively, by highlighting the conversion process of Pb(II) to Pb(IV) by either Mn(VII) or MnO₂, the reactive Pb(III) intermediates were proposed to account for the Pb(II) enhancement effect.     

Advances in Fe(III) bioreduction and its application prospect for groundwater remediation: A review

Microbial Fe(III) reduction is closely related to the fate of pollutants. Bioavailability of crystalline Fe(III) oxide is restricted due to thermodynamics. Amorphous Fe(III) (hydro)oxides are more bioavailable. Enrichment and incubation of Fe(III) reducing bacteria are significant. Microbial Fe(III) reduction is a significant driving force for the biogeochemical cycles of C, O, P, S, N, and dominates the natural bio-purification of contaminants in groundwater (e.g., petroleum hydrocarbons, chlorinated ethane, and chromium). In this review, the mechanisms and environmental significance of Fe(III) (hydro)oxides bioreduction are summarized. Compared with crystalline Fe(III) (hydro)oxides, amorphous Fe(III) (hydro)oxides are more bioavailable. Ligand and electron shuttle both play an important role in microbial Fe(III) reduction. The restrictive factors of Fe(III) (hydro)oxides bioreduction should be further investigated to reveal the characteristics and mechanisms of the process. It will improve the bioavailability of crystalline Fe(III) (hydro)oxides and accelerate the anaerobic oxidation efficiency of the reduction state pollutants. Furthermore, the approach to extract, culture, and incubate the functional Fe(III) reducing bacteria from actual complicated environment, and applying it to the bioremediation of organic, ammonia, and heavy metals contaminated groundwater will become a research topic in the future. There are a broad application prospects of Fe(III) (hydro)oxides bioreduction to groundwater bioremediation, which includes the in situ injection and permeable reactive barriers and the innovative Kariz wells system. The study provides an important reference for the treatment of reduced pollutants in contaminated groundwater.