重金属污染土壤生物毒性的发光菌法测定及评价

向土壤中人为投加重金属污染物,制备了重金属含量不同的一系列污染土壤,对土壤重金属浸提条件进行了探究,并应用明亮发光杆菌T3（Photobacterium phosphoreum T3）对单一Cu、Cd和Pb污染及Cu-Cd和Cu-Pb复合重金属污染土壤的生物毒性进行了测定。实验结果表明,土壤重金属的最佳浸提剂为0.1 mol/L HCl溶液,最佳浸提时间为2.0 h。在单一重金属污染条件下：Cu表现出低浓度促进生长、高浓度抑制生长的双重生物效应,而Cd和Pb则表现出浓度与生物毒性的正相关性;3种重金属污染土壤的毒性强弱顺序为Cd>Pb>Cu。在复合重金属污染条件下,由于重金属之间的相互作用,污染土壤的生物毒性增强。     

重金属污染土壤的修复技术研究进展及发展前景

目前,我国重金属污染呈现出长期积累和近期集中爆发、历史遗留问题和新出现问题相交织的特点,重金属污染在环境中存在多、形态多,整治重金属污染是一项长期、复杂、艰巨的任务.重金属污染物极难降解,尤其是存在于水和土壤中的重金属兼具富集性,是不可逆转的.重点阐述了重金属污染土壤的修复技术研究进展及发展前景.     

喀斯特山区燃煤电厂土壤重金属污染评价

选取地处贵州省喀斯特山区的金沙电厂为研究对象,对电厂周围的表层土壤、蔬菜(莲花白)试样的重金属含量进行了测定,采用模糊数学法对土壤重金属污染进行了评价,采用富集系数法分析了莲花白对重金属的富集能力。实验结果表明:电厂周围表层土壤中Hg,As,Cd,Pb,Cu的平均含量分别达0.70,26.40,0.61,44.83,35.51 mg/kg,其中,Hg和Cd的平均含量分别为GB 15618—1995《土壤环境质量标准》中二级标准的1.40和2.03倍;电厂周围土壤受到较为严重的Hg,As,Cd污染,各个方向的重金属污染程度大小顺序为西北西东南西南东北东,总体趋势为西向大于东向;莲花白对土壤中Cd的富集作用较强,对其他重金属的富集作用较弱。     

土壤重金属污染治理存在的问题及应对措施

随着当前社会各界逐渐提高环保相关意识,土壤重金属污染问题受关注程度越来越高。土壤污染除了会影响整个土壤圈层之外,还会对诸如空气、水体等产生一定程度的污染。土壤重金属污染所涉及的重金属元素主要为Hg,Cd,Pb,Cr,As,Zn,Cu,Ni等。当前治理土壤重金属污染,不仅能够有效提高农产品安全,还能够保证人类的健康发展。分析土壤重金属污染的成因及其对农作物和人类所产生的影响,并尝试从物理、化学、生物等多个角度共同开展修复工作,以求可以为我国受污染土壤开展治理工作提供经验借鉴。     

某污染场地含钒重金属土壤制砖工艺研究

以湖南省某钒工业废弃厂区为研究对象,研究重金属高温烧结深度固化技术,以含钒重金属污染土壤为原料制备烧结砖体。通过添加不同比例的含重金属土壤的处理方法,研究其重金属固化效果、砖力学性质并对比相关标准限值,从而筛选出最优的添加比例。结果显示,当重金属土壤含量达到40%时,固化稳定化效果变差,钒和铜的总量超过《水泥窑协同处置固体废物技术规范》（GB/T 30760—2014）中规定的限值,故针对研究对象建议采用添加比例不超过30%进行烧结制砖,可保证资源化利用的同时,避免原位处理潜在的二次污染。研究结果为含钒重金属污染土壤建立了一套行之有效的资源化、无害化处置的工艺流程,为促进土壤污染修复产业的形成与发展提供借鉴。     

万山汞矿区土壤重金属污染特征及来源解析

以万山汞矿区土壤为研究对象,采用电感耦合等离子体质谱仪和原子荧光光谱仪测定土壤中的重金属含量,分别运用内梅罗综合污染指数（NPI）法和潜在生态风险指数（RI）法评价土壤重金属污染和潜在生态风险,并应用相关性分析、主成分分析和聚类分析对土壤重金属来源进行分析。结果表明：土壤Hg、Cd、As、Pb、Cu、Ni和Zn出现不同程度累积,分别达贵州省背景值的263.61、2.31、1.28、2.11、1.70、1.01和3.52倍;土壤重金属平均NPI为188.00,属于严重污染水平,Hg是主要污染因子;土壤重金属平均RI为10 655.70,属于极强潜在生态风险水平,Hg是主要潜在生态风险因子;土壤中Cu、Ni、Cr主要源于自然活动,As、Pb、Zn主要源于燃煤和交通运输污染,Cd主要源于农业污染,Hg主要源于汞冶炼污染。     

重金属镉污染下石榴的耐性特征及重金属富集研究

土壤是人类生产和生活中不可或缺的生存资源,但随着工业革命和科学技术的快速发展,重金属污染也越来越难以控制和消除。重金属进入土壤,会对其中的动植物造成严重的损害,甚至可能污染地下水,造成严重的经济损失。为了人类的健康和环境可持续发展,重金属污染的修复和治理已势在必行。通过对重金属镉污染下石榴的耐性特征及重金属富集研究,探究重金属对植物的影响机制。     

丛枝菌根真菌-植物修复矿区重金属污染土壤的研究进展

阐述了丛枝菌根真菌(AMF)-植物对重金属污染土壤的修复机制,重点介绍了AMF-植物联合技术在金属矿区、煤矿区重金属污染土壤修复中的应用,并对今后该技术的发展和应用前景进行了展望。指出:加大AMF-植物联合修复技术的研究和实践,将会带来更好的经济效益和环境效益。     

环境重金属污染的生物指示作用

针对指示生物在环境重金属污染监测、评价与防治中所起的指示作用与研究现状,介绍了有关指示生物的基本理论,分析了常见指示生物对土壤、水和大气环境重金属污染的指示作用。提出了选择合适的指示生物是发挥其对重金属污染指示作用的关键。最后,提出了指示生物对环境重金属污染指示作用的局限性及对策。     

复合重金属污染高岭土的电动修复

根据电子废弃物拆解场地的污染特征,以复合重金属(Cu,Cd,Pb)污染高岭土为研究对象,考察了电动技术对污染土壤的修复效果。实验结果表明:在电压梯度为1 V/cm、阳极液为自来水、阴极液为柠檬酸-柠檬酸钠缓冲液(pH=5)、靠近阴极设置活性炭渗透反应墙(PRB)的条件下电动修复96 h后,Cu,Cd,Pb的平均去除率分别可达79.93%,99.43%,39.36%;土壤的酸碱性对电动修复效果影响显著,通过在阴极添加缓冲液维持土壤偏酸性条件,有利于重金属污染物的电动去除;在靠近阴极设置活性炭PRB可富集重金属,减少阴极液的污染;迁移率大的酸可提取态重金属较易去除,残渣态重金属稳定性强,去除率较低。     

Cement clinker: An environmental sink for residues from hazardous waste treatment in cement kilns

About 70% of all of the liquid and solid hazardous wastes commercially incinerated in the United States is being burned in cement kilns. The process inevitably results in residues, primarily heavy metals, entering the clinker and waste dusts (cement kiln dust, CKD) produced by these kilns. The effects of this trend on the nature and chemical composition of cement, actual and future, are discussed. The wastes burned by cement kilns are expected to increasingly have higher levels of heavy metals per Btu. In general, the effects are very simple to describe but have as yet unknown consequences. The present American Society for Testing and Materials (ASTM) standard does not effectively control hazardous waste burning residues in Portland Cement.The regulatory and economic pressures on CKD disposal suggest that much of it, and its heavy metal residues, will, in time, end up in the clinker and the resultant cement. The end point to the trend is the ability to make cement that passes the performance specifications while containing high levels of heavy metals. The only other alternative is to maximize the levels of heavy metals in the CKD, minimize the amount of CKD, and dispose of its as a hazardous waste.It is recommended that an effort to correlate heavy metal levels in clinker with adverse effects be undertaken, a new standard for cement containing hazardous and other waste residuals be developed, and labeling be required.     

Immobilisation of heavy metal in cement-based solidification/stabilisation: a review

Heavy metal-bearing waste usually needs solidification/stabilization (s/s) prior to landfill to lower the leaching rate. Cement is the most adaptable binder currently available for the immobilisation of heavy metals. The selection of cements and operating parameters depends upon an understanding of chemistry of the system. This paper discusses interactions of heavy metals and cement phases in the solidification/stabilisation process. It provides a clarification of heavy metal effects on cement hydration. According to the decomposition rate of minerals, heavy metals accelerate the hydration of tricalcium silicate (C3S) and Portland cement, although they retard the precipitation of portlandite due to the reduction of pH resulted from hydrolyses of heavy metal ions. The chemical mechanism relevant to the accelerating effect of heavy metals is considered to be H+ attacks on cement phases and the precipitation of calcium heavy metal double hydroxides, which consumes calcium ions and then promotes the decomposition of C3S. In this work, molecular models of calcium silicate hydrate gel are presented based on the examination of 29Si solid-state magic angle spinning/nuclear magnetic resonance (MAS/NMR). This paper also reviews immobilisation mechanisms of heavy metals in hydrated cement matrices, focusing on the sorption, precipitation and chemical incorporation of cement hydration products. It is concluded that further research on the phase development during cement hydration in the presence of heavy metals and thermodynamic modelling is needed to improve effectiveness of cement-based s/s and extend this waste management technique.     

典型磷矿区表层土壤重金属空间分布特征研究

以开阳磷矿区为对象,结合地统计学普通克里金插值法以及单因素分析法,研究了矿区表层土壤重金属的空间分布特征,并对其进行了污染评价。结果表明：以矿区当地土壤重金属背景值为标准,Cu,Zn,Pb,Cd,As含量均存在超标情况;5种元素含量的变异程度均为高度变异,Pb,Cd,As的变异系数远大于Cu,Zn的变异系数;土壤重金属空间分布特征为Cd,As含量在东北部的积累程度大于西南部,东北—东南方向Cu,Zn,Pb,Cd,As的富集程度远大于西北—西南方向;不同土地利用类型对重金属的积累没有显著影响,这很可能与其他因素如背景值、风向、人类干扰（如化工产业）等有关。     

气化炉渣的重金属浸出特性及化学形态分析

分别采用硫酸硝酸法、水平振荡法和醋酸缓冲溶液法制取气化炉渣的浸出液,考察了不同提取方式对浸出液中重金属质量浓度的影响。采用改进BCR连续提取法对气化炉渣中的重金属Cr,Zn,Cu,Pb,Ni,As,Cd的化学形态进行了分析。实验结果表明：煤气化工艺中的气化炉渣属第Ⅰ类一般工业固体废物;在3种提取方式中,醋酸缓冲溶液法的重金属浸出种类最多,且浸出量最大;Cd和Cr对环境具有较高的潜在危害性,Cu次之,Zn,Pb,Ni,As主要以残渣态形式存在,对环境的直接危害性较低。     

硫酸锰渣污染土壤中重金属的形态分布及生物活性

测定了硫酸锰渣污染土壤中Cu,Zn,Cd,Pb,Mn的总量和各形态含量.结果表明重金属总量远超过环境背景值和土壤环境二级标准.重金属各形态分布特征:Cu,有机态>残渣态>铁锰氧化态>碳酸盐态>可交换态;Zn,残渣态>铁锰氧化态>有机态>碳酸盐态>可交换态;Cd,铁锰氧化态>可交换态>碳酸盐态>残渣态>有机态;Pb,铁锰氧化态>残渣态>有机态>碳酸盐态>可交换态;Mn,铁锰氧化态>残渣态>可交换态>有机态>碳酸盐态.重金属的生物可利用性系数和迁移系数均为Cd>Mn>Pb>Cu>Zn.     

我国石煤提钒废水的处理现状与展望

石煤提钒废水中含有大量的重金属、氨氮和盐类。介绍了石煤提钒中重金属废水、氨氮废水、高盐废水的处理技术,总结了各种废水处理技术在石煤提钒废水治理中的应用现状,并对石煤提钒废水的治理进行了展望。化学法应用广泛,但易造成二次污染;物理法具有广阔的应用前景,但处理效率低;生物法具有效率高、选择性强、废水处理成本低等优点,是一种极具发展潜力的废水治理方法,应加大在石煤提钒废水治理方面的研究。     

Influence of calcium chloride on the thermal behavior of heavy and alkali metals in sewage sludge incineration

In order to separate and reuse heavy and alkali metals from flue gas during sewage sludge incineration, experiments were carried out in a pilot incinerator. The experimental results show that most of the heavy and alkali metals form condensed phase at temperature above 600 degrees C. With the addition of 5% calcium chloride into sewage sludge, the gas/solid transformation temperature of part of the metals (As, Cu, Mg and Na) is evidently decreased due to the formation of chloride, while calcium chloride seems to have no significant influence on Zn and P. Moreover, the mass fractions of some heavy and alkali metals in the collected fly ash are relatively high. For example, the mass fractions for Pb and Cu in the fly ash collected by the filter are 1.19% and 19.7%, respectively, which are well above those in lead and copper ores. In the case of adding 5% calcium chloride, the heavy and alkali metals can be divided into three groups based on their conversion temperature: Group A that includes Na, Zn, K, Mg and P, which are converted into condensed phase above 600 degrees C; Group B that includes Pb and Cu which solidify when the temperature is above 400 degrees C; and Group C that includes As, whose condensation temperature is as low as 300 degrees C.