Review on utilization of biochar for metal-contaminated soil and sediment remediation

Biochar is a carbon-neutral or even carbon-negative material produced through thermal decomposition of plant- and animal-based biomass under oxygen-limited conditions. Recently, there has been an increasing interest in the application of biochar as an adsorbent, soil ameliorant and climate mitigation approach in many types of applications. Metal-contaminated soil remediation using biochar has been intensively investigated in small-scale and pilot-scale trials with obtained beneficial results and multifaceted effects. But so far, the study and application of biochar in contaminated sediment management has been very limited, and this is also a worldwide problem. Nonetheless, there is reason to believe that the same multiple benefits can also be realized with these sediments due to similar mechanisms for stabilizing contaminants. This paper provides a review on current biochar properties and its use as a sorbent/amendment for metal-contaminated soil/sediment remediation and its effect on plant growth, fauna habits as well as microorganism communities. In addition, the use of biochar as a potential strategy for contaminated sediment management is also discussed, especially as regards in-situ planning. Finally, we highlight the possibility of biochar application as an effective amendment and propose further research directions to ensure the safe and sustainable use of biochar as an amendment for remediation of contaminated soil and sediment.     

Rhizophagus irregularis influences As and P uptake by alfafa and the neighboring non-host pepperweed growing in an As-contaminated soil

It was documented that arbuscular mycorrhiza fungi(AMF) play an important role in protecting host plants against arsenic(As) contamination. However, most terrestrial ecosystems contain a considerable number of nonmycorrhizal plants. So far little information is available for the interaction of such non-host plants with AMF under As contaminations. By using a dual compartment cultivation system with a plastic board or a nylon mesh separating roots of non-host pepperweed from roots of the AM-host alfafa plants, avoiding direct root competition, the two plant species were grown separately or partially separated(with rhizosphere effects) in the presence or absence of the AMF Rhizophagus irregularis in As-contaminated soil. The results indicated that mycorrhiza caused phosphorus(P) concentration decrease in the non-host pepperweed, but promoted the P concentration of the AM host alfafa. Mycorrhiza is potentially helpful for non-host pepperweed to adapt to As contamination by decreasing root As concentration and showing no suppressing effect on biomass production. The study provides further evidence for the protective effects of AMF on non-host plants against As contamination, and improved our understanding of the potential role of AMF for non-host plant adaptation to As contaminated soils.     

Microbial methylation of mercury in the water-level fluctuation zone of the Three Gorges Reservoir, China

正Methylmercury(MeHg)is an organic form of the global pollutant mercury(Hg)which readily accumulates in fish tissue.A majority of Hg methylation is a result of microbial activity and the abundance of inorganic Hg within the water reservoirs(Eckley et al.,2017).Compared to natural lakes and rivers,reservoirs have elevated Hg levels from the decomposition of recently flooded organic material which promote Hg     

三峡库区消落带农业活动对土壤汞变化的影响

针对三峡库区消落带退水期农业生产是否会对库区环境带来不利影响的问题,以分布面积较大、农业活动较为频繁的重庆市开州区渠口镇消落带为研究区域,选择种植水稻、玉米、蔬菜和未农用的草地4类消落带地块为研究对象,调查了不同利用地块表层土壤汞(Hg)的变化特征.结果表明,研究区域内土壤THg、有效态Hg(Hg-wh)和甲基汞(MeHg)平均含量分别为25.80~68.74、0.44~0.88和0.08~0.85 ng·g-1.未耕作土地表层土壤THg、Hg-wh和MeHg含量均高于耕作土地表层土壤,说明耕作扰动能够加速土壤Hg的流失.未耕作土壤与耕作土地表层土壤MeHg含量随着落干时长的增加均呈现先升高后降低的趋势,峰值大约出现在落干后1~2个月内,约为淹水末期的4倍,之后逐渐降低至相对稳定的水平.MeHg占THg比例(%MeHg)也呈现类似规律,峰值出现在落干后1个月左右,降到稳定水平时与淹水末期含量无显著性差异(P0.05).土壤%MeHg与Hg-wh含量呈显著性正相关关系(r=0.642,P0.01),而与THg含量没有显著相关性(P0.05),说明消落带土壤Hg甲基化主要受生物可利用性Hg形态的影响.     

采油井场土壤微生物群落结构分布

为了评价采油井场石油污染的微生物修复潜力,选取油井旁持续污染区(W)、井场曾经污染区(S)、原泥浆池区(M)和周边农田区(F)这4个不同位置,对0~400 cm不同深度土壤进行调查取样.利用高通量测序技术,对样品16S rRNA基因V4区序列进行测定,结合石油含量、三氮等物化性质,分析了微生物的生物多样性、群落组成及其和环境因子的关系.结果表明,石油污染减少了土壤的生物多样性,石油含量、盐度是造成微生物群落结构差异的最主要环境因子.通过组间差异分析发现,W和M土壤不仅存在着大量的石油降解细菌,其中的高盐样品中还含有嗜盐石油降解古菌.S与F具有相似的群落结构,表明石油烃的自然衰减.因此,该井场具有丰富的石油修复菌种资源,具有很好的微生物修复潜力.     

三峡库区涪陵和忠县两地居民发汞含量水平及影响因素分析

为评价三峡库区居民汞暴露风险,在三峡库区腹心地带的涪陵和忠县两地采集了238份当地居民头发样本,分析了总汞(THg)和甲基汞(Me Hg)含量.结果表明,两地居民头发THg、Me Hg平均含量分别为(0.50±0.54)μg·g~(-1)、(0.35±0.25)μg·g~(-1).其中,涪陵居民头发THg、Me Hg平均含量分别为(0.71±0.87)μg·g~(-1)、(0.53±0.46)μg·g~(-1),均高于忠县居民头发THg[(0.41±0.36)μg·g~(-1)]、Me Hg[(0.28±0.26)μg·g~(-1)]平均含量水平,但两地头发总汞平均含量均低于美国EPA安全参考剂量(1μg·g~(-1)).不同年龄段的居民发汞含量存在显著性差异(P0.05),其中40~50岁年龄段居民发汞含量最高;不同性别间发汞含量差异不显著(P0.05),但女性发汞含量略高于男性.居民发汞含量与食鱼频率呈正相关,渔民发汞含量显著高于非渔民发汞含量(P0.01),且渔民头发样本总汞含量均值(1.44±0.79)μg·g~(-1)超过了EPA安全参考剂量.两地吸烟者头发总汞含量[(0.55±0.24)μg·g~(-1)、(0.58±0.54)μg·g~(-1)]均显著高于非吸烟者头发总汞含量[(0.51±0.30)μg·g~(-1)、(0.36±0.26)μg·g~(-1)].三峡库区居民汞暴露风险总体较低,但渔民存在一定的汞暴露风险.     

藻类在水体污染监测中的运用

利用藻类进行水体污染监测在水生生物监测中占有重要的地位。各种不同的水体污染对藻类的种类,数量,结构等产生相应的影响,在一定程度上表明了水质的某种变化。     

山地土壤—植物系统中汞污染问题的初步调查

调查研究表明：在山地大气、水体质量较好的环境中,柑橘（含汞量）有超标问题,其土壤汞有超背景值现象;而蔬菜土壤则无此问题,其原因可能是由于多年生植物从大气和土壤中富积微量汞的时间较一年生植物长,以及土壤中砂粒结合汞粘粒结合汞具有更高的生物活性     

山东省主要果园土壤中Cu、Zn的形态、含量及分布

对我国山东省主要果园土壤中的Cu、Zn元素的形态、含量及分布进行了研究。结果表明 :果园土壤中Cu、Zn元素的全量高于一般粮田土壤。在不同土壤类型中 ,形态分布各具特点 ,Cu元素在棕壤和褐土中的形态分布趋势一致 ,为矿物态 >有机态 >沉淀态 >交换态 ,在潮土和砂姜黑土中一致 ,为矿物态 >沉淀态 >有机态 >交换态 ;而Zn元素在这 4种土壤中的分布趋势相同 ,均为矿物态 >沉淀态 >有机态 >交换态。土壤中交换态的Cu、Zn含量随土壤pH值的增大而减小。Cu、Zn某些形态的含量与土壤中全量间有一定的相关性 ,其中沉淀态Cu与总Cu的关系较为紧密 ,2者呈极显著相关 ;矿物态Zn与总Zn也呈极显著相关。     

汞和硒对剑尾鱼Na+/K+-ATPase活性的影响

应用浸浴法研究汞(Hg)对剑尾鱼(XiphophorushelleriHeckel)鳃和肝脏Na /K ATPase活性的影响以及硒(Se)对机体Na /K ATPase汞中毒的保护作用.结果表明,Hg和Se对剑尾鱼96hLC50分别为0.84mg/L和6.64mg/L.Hg对剑尾鱼鳃和肝脏Na /K ATPase活性的影响相似,与对照组相比,处理d1时低浓度Hg组鳃和肝脏ATPase活性没有明显变化(P>0.05),但高浓度Hg组ATPase活性变化显著(P<0.05),至d3和d5时,酶活性均极显著下降(P<0.01),鱼鳃和肝脏酶活性分别下降32%和60%,表明Hg处理对鳃和肝脏Na /K ATPase活性具有抑制作用.单独加Se组鱼鳃和肝脏Na /K ATPase活性在d3和d5显著提高(P<0.01).Hg Se组与Hg组相比,酶活性有明显差异(P<0.05或P<0.01),Se对剑尾鱼Hg中毒具有保护作用.剑尾鱼鳃和肝细胞Na /K ATPase活性可作为对水环境汞污染效应环境风险评价(ERA)的有效生物学标记.表2参16