包埋固定化微生物厌氧反应器启动特性研究

为克服难降解废水厌氧微生物反应器启动初期生物易流失和启动过程缓慢的缺点,将厌氧絮状污泥进行固定化包埋作为厌氧反应器的接种污泥处理有毒难降解的PTA废水,同时考察固定化细菌在厌氧反应器启动过程中的变化特性.结果表明,经过136 d的运行,反应器在COD有机负荷为3 kg.(m3.d)-1,水力停留时间为3~4 d的运行条件下,PTA废水的COD去除率可以达到75%~85%,且系统具有比较好的稳定性和生物量保持能力.另一方面,胞外聚合物(EPS)的变化、产甲烷菌DNA特异性扩增和包埋颗粒的扫描电镜观察结果表明,虽然包埋载体在一定程度上限制了传质速度,但包埋颗粒中的厌氧微生物在微生物相和数量上都仍有显著的变化和增长.     

十二烷基磺酸钠(SDS)改性蒙脱石对Cu~(2+)、Cd~(2+)的吸附研究

以阴离子表面活性剂(十二烷基磺酸钠,SDS)为改性剂制备了有机蒙脱石,研究其对Cu2+、Cd2+的吸附行为,并用XRD、FTIR、SEM、XPS对有机蒙脱石进行表征.实验结果表明,有机蒙脱石对Cu2+、Cd2+的吸附基本上在20min内达到平衡,并随pH增大(1.0～7.0),吸附量增加,最佳pH约为6.0.有机蒙脱石对Cu2+、Cd2+的吸附等温线更符合Langmuir等温吸附方程,SDS改性蒙脱石对Cu2+、Cd2+的最大吸附量较纯蒙脱石分别增加15.7%、15.5%.XRD、FTIR、SEM、XPS及碳含量分析结果显示,SDS主要分布在蒙脱石表面且相对稳定,少量嵌入层间,有机蒙脱石对Cu2+、Cd2+的吸附机制为配位吸附和离子交换.     

表面覆膜多层复合纤维滤料过滤性能的数值研究

根据Matlab软件和数值计算前处理软件Gambit中的Journal文件建立了多层复合纤维滤料模型,利用计算流体动力学(CFD)技术对沿气流方向具有不同纤维填充密度及直径分布的滤料内部的气-固两相流动特性进行了数值研究,计算了不同运行条件下滤料的压力损失及过滤效率,并将数值计算值和经典模型及实验关联式的计算值进行了比较.结果表明,压力损失的数值计算预测值和实验关联式计算值吻合较好,误差在2%以内.随着迎面风速的增加,压力损失呈线性增加.相对于填充密度,纤维直径对压力损失和过滤效率的影响更显著.不同结构滤料过滤效率的数值计算结果和理论模型的计算值变化趋势基本一致.不同迎面风速下,过滤效率都是先减小后增大,对于颗粒直径dp≤0.05μm的颗粒,随着风速的增大,过滤效率减小;对于dp≥0.5μm的颗粒,过滤效率变化趋势正好相反.迎面风速不同,过滤效率最低点出现的位置也不同.对于小颗粒,风速越小,扩散作用起主导作用;而对于大颗粒,风速越大,惯性作用越明显.过滤效率最低点出现在扩散作用逐渐弱化,惯性作用刚刚开始加强的区域.多层复合滤料在结构上采用纤维直径逐层加大的梯次结构时,能够获得较高的过滤效率.而在多层复合滤料表面覆膜后过滤效率平均增加约13%.     

复合生态滤床用于重金属污染地表水体修复

以蛭石为滤床基质,研究了复合生态滤床对受重金属污染地表水体的修复效能.结果表明,复合生态滤床对重金属污染水体有较好的处理效果,在水力负荷为2.0m.3m-.2d-1时,系统对Cu、Zn、Pb和Cd的平均去除率分别达到81.60%、80.55%、83.20%、62.21%;按照国家《地表水环境质量标准》(GB3838-2002),出水重金属浓度达到Ⅱ类水质标准;出水COD值为9.7～38.3mg·L-1,达到Ⅰ类水质标准;出水NH4+-N达到1mg·L-1以下,达到Ⅲ类水质标准.滤床基质中铜离子含量稳定在30mg·kg-1左右,表明植物根系可以有效地吸收蛭石吸附的重金属,从而有效提高蛭石的再吸附能力,延长滤床工作周期.     

生态工程在水污染控制中的应用

生态工程可简单定义为"通过自然系统或人工仿自然系统的生态过程来达到生态目的"。与环境工程相比,更符合可持续发展要求,因此在水污染控制方面受到越来越多的关注。本文主要介绍了土地处理系统、蚯蚓-微生物生态滤池、生态浮岛等生态污水处理技术及其在工程中的应用。     

固定化光催化技术及其适用水处理反应器研究进展

光催化技术因其较高的催化活性和低廉的价格已经被水处理业内广泛采用．但是粉末催化剂的明显缺点制约了其工业化应用,因此固定化光催化技术应运而生。通过收集国内外资料．对于光催化固定技术应用的两个关键因素——固定方法和适用的反应器的发展进行了介绍。当固定的同时催化剂活性不大幅下降．且采用适合于该种载体的反应器,固定化光催化技术在水处理领域有着广阔的应用前景。     

F/M对ASBR中基质的吸收、储存和利用影响

研究了不同F/M（COD/VSS）下以葡萄糖为基质时厌氧序批式反应器（ASBR）中的微生物代谢规律.结果表明,在序批操作条件下,水解产酸菌对葡萄糖的代谢存在2条并列的途径,即直接代谢为VFA和首先转化为胞内储存物糖原,然后糖原再被转化为VFA.前者约占进水COD的34%～38%,而后者则高达41%～46%.F/M越高,糖原的储存量越大,当F/M分别为0.27、 0.20和0.14时,单位质量污泥糖原的最大储存量分别为116.8、 81.1和62.4 mg/g.糖原的储存减缓了VFA的积累,为ASBR反应器的高效和正常运行创造了条件.     

A/A系统反硝化除磷的强化及其稳定性研究

利用厌氧/缺氧(A/A)SBR,试验研究了选择和富集反硝化除磷菌(DPB)的条件.结果表明,采用电子供体和电子受体充分分开的两段进水方式运行,当厌氧段进水COD与缺氧段投加硝酸盐质量浓度为300 mg.L-1、50 mg.L-1,pH值约为7.0时,DPB可快速成为系统中的优势菌群,系统可达到良好的反硝化聚磷效果;将前述系统改变为一段进水方式运行后,系统仍具有良好的反硝化聚磷效果.在进水磷浓度同为20 mg.L-1下,在缺氧段投加磷的运行方式比在厌氧段投加磷的运行方式更能提高系统的除磷能力.     

Mass transfer in the absorption of SO2 and NOx using aqueous euchlorine scrubbing solution

Attempts have been made to generate euchlorine gas by chlorate-chloride process and to utilize it further to clean up SO2 and NOx from the flue gas in a lab scale bubbling reactor.Preliminary experiments were carried out to determine the gas and liquid phase mass transfer coefficients and their correlation equations have been established.Simultaneous removal of SO2 and NOx from the simulated flue gas using aqueous euchlorine scrubbing solution has been investigated.Euchlorine oxidized NO into NO2 completely and the later subsequently absorbed into the scrubbing solution in the form of nitrate.SO2 removal efficiency of around 100% and NOx removal efficiency of around 72 % were achieved under optimized conditions.Mass balance has been confirmed by analyzing the sulfate, nitrate, euchlorine and chloride ion using ion chromatograph/auto-titrator and comparing it with their corresponding calculated values.     

Nitrogen removal via nitrite from municipal landfill leachate

A system consisting of a two-stage up-flow anaerobic sludge blanket (UASB), an anoxic/aerobic (A/O) reactor and a sequencing batch reactor (SBR), was used to treat landfill leachate. During operation, denitrification and methanogenesis took place simultaneously in the first stage UASB, and the e uent chemical oxygen demand (COD) was further removed in the second stage UASB. Then the denitrification of nitrite and nitrate in the returned sludge by using the residual COD was accomplished in the A/O reactor, and ammonia was removed via nitrite in it. Last but not least, the residual ammonia was removed in SBR as well as nitrite and nitrate which were produced by nitrification. The results over 120 d (60 d for phase I and 60 d for phase II) were as follows: when the total nitrogen (TN) concentration of influent leachate was about 2500 mg/L and the ammonia nitrogen concentration was about 2000 mg/L, the shortcut nitrification with 85%–90% nitrite accumulation was achieved stably in the A/O reactor. The TN and ammonia nitrogen removal e ciencies of the system were 98% and 97%, respectively. The residual ammonia, nitrite and nitrate produced during nitrification in the A/O reactor could be washed out almost completely in SBR. The TN and ammonia nitrogen concentrations of final e uent were about 39 mg/L and 12 mg/L, respectively.