煤体灰分与挥发分对煤吸附甲烷性能的影响实验研究

为研究煤体灰分、挥发分对煤吸附甲烷性能的影响,运用高容量吸附装置测定同一煤矿不同灰分、挥发分煤样的等温吸附曲线和吸附常数a、b值,并运用SPSS多元线性回归软件进行分析。实验结果表明:不同灰分、挥发分煤样的等温吸附曲线符合Langmuir方程,且二者对于煤吸附甲烷性能均有一定的影响。煤灰分不变时,吸附常数a值随挥发分的增大而线性递增,吸附常数b值随挥发分的增大而线性递减;煤挥发分不变时,a值随灰分的增大而线性递增,b值随灰分的增大而线性递减。研究结果为准确测定煤层瓦斯含量、瓦斯压力等参数提供了一定的理论依据。     

结晶紫在乙酸膨润土上的吸附行为

采用乙酸膨润土(AAB)研究其对水体中结晶紫(CV)染料的吸附.结果表明,投加量为0.8 g/L时吸附500 mg/L的CV即可达到99％的去除率;随着染液pH值的上升,AAB对CV的去除率呈现逐渐提高趋势,AAB吸附CV的适宜pH值范围较宽广,pH值为5～10时,去除率均可达80％以上,pH值为11时去除效果达到最高,可迭99％;低于0.1 mol/L的NaC1会促进CV的吸附,高于0.1 mol/L的NaCl会抑制对CV的吸附;AAB吸附CV可达到99％的去除率,其平衡吸附时间为180 min;温度升高可以增加吸附容量,但增加不明显;其吸附动力学过程符合准二级动力学模型;CV在AAB上的吸附符合Langmuir模型,计算得到Langmuir吸附容量为1000 mg/g.     

改良ABR处理农村生活污水动力学研究

通过改良ABR(厌氧折流板反应器)处理农村生活污水试验表明:在不同HRT(水力停留时间)、有机负荷、温度的运行条件下,污泥沉降速率平均值分别为59、61、58 m/h,污泥具有良好的沉降效果;ρ(COD_(Cr))沿隔室递减,去除率最高达88%;反应区隔室沿程的MLVSS/MLSS(混合液挥发性悬浮固体浓度/混合液悬浮固体浓度)值为0.63、0.65、0.65,生物含量较高。在此基础上构建改良ABR基质降解动力学模型,模型计算值与实测值误差在0.1%之内,表明构建模型合理,为ABR优化设计提供了借鉴。     

固定化生物活性炭技术处理模拟铅锌矿山酸性废水

从湖北大冶某铅锌矿选矿废水排水沟污泥中驯化筛选出1株能够有效吸附Zn²⁺、Pb²⁺并耐低pH值的菌株T1,经分子生物学鉴定,其为芬氏纤维微菌（Cellulosimicrobium funkei）。将T1按单菌种连续挂膜法固定在活性炭上,采用固定化生物活性炭（Immobilized Biological Activated Carbon,IBAC）技术处理pH=4、Pb²⁺含量为30 mg/L、Zn²⁺含量为100 mg/L的模拟铅锌矿山酸性废水,并与单纯活性炭吸附工艺进行对比,试验结果表明：IBAC工艺对模拟废水中Zn²⁺、Pb²⁺的7 d平均去除率分别达75.28%和74.16%,处理后废水的pH值提高至6.8~7.5;单纯活性炭吸附工艺虽然在处理模拟废水的开始阶段可取得高达96.80%和95.21%的Pb²⁺、Zn²⁺去除率,但80 h后Pb²⁺、Zn²⁺的去除率分别下降到只有9.65%和12.93%,而IBAC工艺的Pb²⁺、Zn²⁺去除率始终保持在68.27%~76.25%和71.27%~77.89%的较高水平。扫描电镜捡测结果显示：活性炭挂膜后颗粒表面被T1覆盖,变得更为粗糙,孔隙更多;T1呈纤维状,吸附Pb²⁺、Zn²⁺后体积膨胀,相互间黏结性更强。以上研究成果可为IBAC技术处理铅锌矿山酸性废水的工业化提供参考。     

吸附与混凝联用去除水中磷的特性研究

为了解决粉煤灰高效除磷但不易与水分离的问题,将粉煤灰吸附与聚合硫酸铁（PFS）混凝联用来处理含磷污水,采用单因素法考察了PFS投加量、粉煤灰投加量、振荡强度、PFS投加点、pH值、氨氮存在时对磷的去除率影响。结果表明：当初始磷质量浓度为2 mg/L时, PFS投加量30 mg/L,粉煤灰投加量20 g/L,振荡强度50 r/min,PFS在粉煤灰吸附20 min后加入,pH值中性,无氨氮存在时,反应30 min磷去除率为75.85%;氨氮存在对磷去除率有一定促进作用;粉煤灰吸附与聚合硫酸铁（PFS）混凝联用可有效处理含磷污水。     

铝盐改性石英砂制备及其吸附性能研究

以石英砂为载体,用反复加热蒸干法制备了铝盐改性砂,分别考察了铝盐改性砂对有机物和Zn2+的吸附性能及其影响因素.结果表明,在pH值为中性条件下,铝盐改性砂吸附效果优于石英原砂,铝盐改性砂对CODCr的去除率比石英原砂提高20%.对UV254的去除率提高了10%左右;铝盐改性砂对Zn2+去除能力比原砂有较大的提高,在pH值中性条件下,石英原砂Zn2+的去除率为43%左右,铝盐改性砂对Zn2+去除率达到70%;随着Zn2+初始浓度的增大,铝盐改性砂对Zn2+的去除率逐渐减少;当改性剂浓度逐渐增大时,Zn2+的去除率逐渐增大,当浓度达到1.25mol/L后,Zn2+的去除率不再提高;铝盐改性砂对Zn2+的去除率随着pH值的升高而提高,当pH值为9时,去除率达90%.     

淮南煤及其燃烧产物中稀土元素丰度的比较

运用ICP-MS测定了51件淮南煤及其燃烧产物中稀土元素的含量,并对煤及其阶段燃烧产物的稀土元素含量进行了比较.研究表明：① 淮南煤中ΣREE平均值为133.09 μg/g,LREE/HREE平均值为2.47,具轻稀土富集、重稀土亏损的分布特征;②低温（815 ℃）煤灰中ΣREE=491.47～2 822.53 μg/g,平均值950.24 μg/g;与“北美页岩”（NASC）相比,煤灰中ΣREE平均含量为背景值的4.27倍;③ 与煤中稀土元素的含量相比,淮南煤中REE在低温燃烧过程中平均散逸程度为11.97％,其中,LREE和HREE的散逸程度分别为12.30％和11.75％;元素分布中,以Eu和Yb的散逸程度最高.煤灰中稀土元素在低温到高温（1 100 ℃）阶段燃烧过程中,REE元素基本无聚集,无散逸.     

赤泥基非均相催化剂类Fenton催化降解金橙Ⅱ

采用糖蜜酒精废液协同H2SO4对赤泥进行酸化改性,再经高温焙烧处理,得到赤泥基非均相催化剂（SMA-CA/赤泥）,通过XRD、EDS、N2吸附脱附技术对SMA-CA/赤泥进行了表征,并将其用于金橙Ⅱ的类Fenton催化降解。表征结果显示：经酸化和焙烧,赤泥中的α-FeOOH转变为SMA-CA/赤泥中的α-Fe2O3,且酸化改性使得SMA-CA/赤泥碱含量显著降低;与未添加糖蜜酒精废液酸化改性的赤泥基非均相催化剂相比, SMA-CA/赤泥的孔径增大,大孔分布提高。实验结果表明：在初始溶液pH值为3、H2O2投加量50 mmol/L、金橙Ⅱ质量浓度40 mg/L、反应时间6 h的条件下,金橙Ⅱ去除率达到86.79%;该催化降解过程符合一级动力学模型。     

污泥厌氧发酵-硫酸盐还原菌耦合体系产电性能和处理酸性矿井水的研究

为原位治理高硫煤矿区酸性矿井水,建立微生物燃料电池污泥厌氧发酵-硫酸盐还原菌耦合体系,考察了电极类型、阳极面积、极间距、离子浓度对产电性能和处理酸性矿井水中的硫酸盐效果的影响。单因素试验结果表明,碳布为阳极、极间距适中(3 cm)时,产电最佳;阳极面积越小、NaCl浓度越高,功率密度越大;硫酸根去除率的最佳条件为：碳布为阳极、极间距为5 cm、离子浓度适中,阳极面积越大,对硫酸根去除率越高。以硫酸盐去除最佳条件构建单室无膜碳片为阳极的耦合产电体系,所产生的最大功率密度为2.093 3 mW/m 2,10 d后污泥的COD去除率为43%,废水SO 2-4的平均去除速率达194.4 mg/(L·d -1),最高去除率为64%,比开路时的SO 2-4去除率提高24%。污泥厌氧发酵-硫酸盐还原菌耦合产电体系可同时实现降解剩余污泥和处理含SO 2-4废水。     

耐辐射奇球菌对水中铀（Ⅵ）的吸附试验

为探索治理铀污染的新工艺、新方法,对耐辐射奇球菌吸附铀（Ⅵ）的影响因素进行了研究。结果表明,溶液的pH值、吸附时间和吸附剂投加量对铀去除率影响显著。在含铀（Ⅵ）模拟废水pH=5、吸附时间为180 min、初始浓度为50 mg/L的情况下,投加0.2 g/L的耐辐射奇球菌体吸附剂,铀（Ⅵ）吸附率可达92.30%;随着铀（Ⅵ）初始浓度的提高,铀吸附率微幅下降,吸附量几乎与铀（Ⅵ）浓度成正比。对吸附机理的探讨表明,耐辐射奇球菌对铀（Ⅵ）的吸附行为符合Freundlich等温模型和准二级动力学模型。     

Removal of Metals and Acidity from Acid Mine Drainage Using Municipal Wastewater and Activated Sludge

Co-treatment of acid mine drainage (AMD) and municipal wastewater (MWW) using the activated sludge process is an innovative approach to AMD remediation that utilizes the alkalinity of MWW and the adsorptive properties of the wastewater particulates and activated sludge biomass to buffer acidity and remove metals. The capacity of these materials to treat AMD was investigated in batch mode metal removal tests using high-strength synthetic AMD (pH 2.8, Al 120–200 mg/L, Cu 18–30 mg/L, Fe 324–540 mg/L, Mn 18–30 mg/L, and Zn 36–60 mg/L). Using material from a range of MWW treatment plants, the performance of screened and settled MWW, activated sludges with mixed liquor suspended solids (MLSS) concentrations of 2.0 and 4.0 g/L, and return activated sludges with 6.0 and 7.4 g/L MLSS were compared. Similar trends were observed for the MWW and activated sludges, with removal efficiency generally decreasing in the order Al = Cu > Mn > Zn > Fe. Trends in Fe removal using settled MWW and activated sludges were highly variable, with removal <30 %. Using activated sludges, average removal efficiencies for Al, Cu, Mn, and Zn were 10–65 %, 20–60 %, 10–25 %, and 0–20 %, respectively. Sludge solids concentration was an important controlling factor in metal removal, with removal of Al, Cu, Mn, and Zn increasing significantly with solids concentration. Municipal wastewaters had greater neutralization capacities than activated sludges at high AMD loading ratios. Mixing AMD with screened MWW gave the highest removal efficiency for all metals, achieving average removal of 90–100 % for Al, Cu, and Fe, 65–100 % for Zn, and 60–75 % for Mn. These empirical findings are useful for developing process design parameters in co-treatment systems. Utilizing MWW and activated sludge to remediate AMD can potentially reduce materials and energy requirements and associated costs.     

Removal of Metals and Acidity from Acid Mine Drainage Using Liquid and Dried Digested Sewage Sludge and Cattle Slurry

The metal removal and neutralization capacities of digested sewage sludges from municipal wastewater treatment plants, cattle slurry (liquid manure), and Biofert granules (dried granular anaerobic sludge) were compared under batch conditions using synthetic AMD (pH 2.8) containing high concentrations of Al, Cu, Fe, Mn, Pb, and Zn (100, 15, 270, 15, 2, and 30 mg/L, respectively). The effects of contact time and solids concentration were examined. Metal removal was variable for all materials. Contact time had a significant effect, with total removal often increasing over the experimental time interval (i.e. 30 min to 24 h). Removal efficiency (%) was generally highest for Cu, Pb, and Al, while Mn and Zn were the least removed. Cattle slurry was the best material for metal removal, with the following maximum removals at a solids concentration of 12.9 g/L: Cu >98 %, Al >98 %, Fe >60 %, Mn >18 %, Pb >96 %, and Zn >60 %. Metal removal using digested sewage sludge reached 88 % for Al, 98 % for Cu, 94 % for Pb, and 30 % for Zn. Neutralization was complete within 30 min after AMD was mixed with digested sludges or cattle slurry, with the pH reaching a maximum of 5.5 with the slurry. In contrast, neutralization by the Biofert granules only reached equilibrium after 300 min, and pH remained <4.0 except at high solids concentrations. It appears that recycled waste-derived organic materials can neutralize AMD and remove dissolved metals by adsorption and precipitation, creating a more treatable waste stream or one that could be discharged directly to surface water. Potential methods of safe disposal of metal-enriched organic materials are discussed.     

Acute and Chronic Toxicity of Acid Mine Drainage to the Activated Sludge Process

The combined treatment of acid mine drainage (AMD) and municipal wastewater using the activated sludge process is an innovative approach to AMD remediation. The toxicity of synthetic AMD to activated sludge was evaluated using oxygen uptake rate (OUR) inhibition tests, which showed that activated sludge can withstand high proportions of AMD (EC₅₀ 19?C52% AMD by volume). The EC₅₀ values of municipal and industrial activated sludges were significantly different (p?<?0.05), with municipal sludges exhibiting higher tolerance to AMD. Although the EC₅₀ values for heterotrophic and nitrifying activated sludges were not statistically significantly different, the EC₅₀ values for heterotrophic bacteria were generally higher. Laboratory-based sequencing batch reactors were used to examine the treatability of AMD. Increased concentrations of COD and suspended solids, associated with turbidity and poor floc morphology, were observed in the final effluent after extended AMD loading. Protozoan community structure changed during the AMD loading period, and overall abundance tended to decrease over time. OUR decreased in the AMD-loaded reactors, particularly in the reactor receiving the highest AMD load, indicating reduced biomass activity over the acclimatization period. Results from OUR inhibition tests on the acclimatized activated sludge indicated that over a relatively short timescale (21?days), the activated sludge microbial community can adapt to AMD sufficiently so that shock loads of metals and acidity do not significantly inhibit OUR. These preliminary studies indicate that it is possible to treat AMD successfully in admixture with municipal wastewater using the activated sludge process.     

Biotreatment of As-containing simulated acid mine drainage using laboratory scale sulfate reducing upflow anaerobic sludge blanket reactor

Heavy metal contamination of water sources can occur from the discharge of acid mine drainage (AMD). This study assessed sulfidogenic treatment of As-, Fe-, Zn-, Ni- and Cu-containing AMD in an upflow anaerobic sludge blanket (UASB) reactor, operated for approximately 500 days. Sulfate reducing granules were successfully enriched with synthetic wastewater and sulfate concentration decreased from 2000 mg/L in the influent to 100–200 mg/L in the effluent. The pH increased from 3–4 to 6–8 as a result of biogenic alkalinity production. Arsenic removal was not detected in the absence of heavy metals, possibly due to the high dissolved sulfide concentration. In the presence of heavy metals, and at low dissolved sulfide concentrations, As removal efficiency increased to 98–100% likely due to the formation of arsenopyrite (FeAsS) or the adsorption of As on metal sulfide precipitates. Fe, Cu, Ni and Zn removal efficiencies approached 99% in the presence of dissolved sulfide. When hydrogen sulfide generation was insufficient to precipitate all of the metals, Fe was detected in the UASB effluent. The results showed that As-, Fe-, Zn-, Ni- and Cu-containing AMD can be effectively treated by sulfate reducing granules in UASB reactors.     

改性煤矸石吸附Cr（VI）的研究

以改性煤矸石对模拟含Cr(VI)废水进行吸附实验。结果表明,在pH值为1.0、吸附时间60min、改性煤矸石用量5g/L时,对进水Cr(VI)为50mg/L的废水进行处理,Cr(VI)的去除率达到99.98%,处理后水样中Cr(VI)含量小于0.50mg/L,达到国家排放标准。利用Freundlich等温式和Langmuir等温式对其吸附进行描述,表明改性煤矸石易于吸附Cr(VI),吸附属于化学吸附。     

尾矿藻-蒙脱石体系吸附模拟废水中Cd(Ⅱ)试验研究

矿山废水含有镉等多种重金属离子,具有高毒性,将其直接排放将对周围水体和土壤造成严重污染并危害人类健康.以蒙脱石和分离自铅锌矿尾矿库的高重金属离子耐受性尾矿藻(Didymogenes palatina XR)形成的体系为研究对象,探究了尾矿藻-蒙脱石体系对模拟含镉废水中Cd(Ⅱ)的吸附效果,利用扫描电镜观察尾矿藻-蒙脱石...     

脂肪酸捕收剂气浮浓缩不同剩余活性污泥的研究

根据矿物浮选原理, 研究了添加脂肪酸捕收剂对3种不同废水处理工艺所产生的剩余污泥气浮浓缩效果的影响。主要考察了捕收剂的种类和用量等因素对不同种类污泥浓缩的影响规律。结果表明, 在3种不同工艺产生的剩余活性污泥中添加脂肪酸捕收剂, 都可以实现污泥的气浮浓缩, 同时降低浓缩污泥的含水率, 极大地改善了气浮浓缩的效果。特别是添加捕收剂ZFS12且用量为75 mg/L时效果最佳, 相对应的3种浓缩污泥的含水率分别为97.26%, 96.64%, 96.44%, 水回收率分别为77.65%, 80.62%, 85.41%。     

磁性膨润土对养牛和养猪沼液的处理性能研究

采用微波共沉淀法合成磁性膨润土(M-Bent),并研究其对养牛和养猪沼液中化学需氧量COD和悬浮物SS的去除效果。M-Bent的XRD、VSM的表征结果表明:磁性Fe3O4纳米颗粒已负载到膨润土上,M-Bent的饱和磁化值为9.41 A·m2/kg,能够成功实现固液分离。吸附实验结果表明:随着M-Bent投加量的增加,对猪、牛沼液中COD和SS的去除率均增大,当投加量为1.0 g/L时,猪沼液中COD和SS的浓度即达到国家标准(GB 18596-2001)的排放要求;由于牛沼液中COD和SS的浓度较高,采用"混凝+吸附"的组合工艺处理牛沼液比单独使用M-Bent吸附的去除效果更佳,并且可达到GB 18596-2001的排放要求。     

高密度底泥回流诱导结晶工艺处理石墨提纯废水

本研究采用高密度底泥回流诱导结晶协同深度除氟工艺处理石墨提纯废水，考察了反应时间、反应pH、底泥回流量对F-去除效果的影响，并比较了普通石灰法与高密度底泥回流两种除氟方式的效果。结果表明，高密度底泥回流诱导结晶工艺处理酸性含氟废水效果良好，在反应时间30min，反应pH7，底泥回流50%条件下，F-可去除至7mg/L，可以达到《污水综合排放标准》（GB8978-1996）一级标准中规定的排放限值。相比于普通石灰法，高密度底泥回流法在相同工况条件下能提高F-去除效果，有效增大污泥颗粒的粒径和污泥密度，沉降性能改善。 并且石灰消耗量下降10.2%，含氟固废减量10.4%，同时有效避免反应沉淀设备结垢。     

改性海藻酸钠凝胶球去除稀土废水中U(VI)

通过一步滴定凝胶法制备了三聚氰胺协同戊二醛改性海藻酸钠复合生物材料(Me@SA/GA),用于稀土废水中U(VI)的去除。结果表明,材料制备上Me@SA/GA的SA:Me最优比例为3:1,当U(VI)初始浓度为5mg/L,pH值为5时,静态吸附试验中,Me@SA/GA投加量0.1g/L,吸附15h,对水中U(VI)的吸附量达到19.75mg/g；动态吸附试验中,以1mL/min的流速过柱,Thomas模型拟合其饱和吸附量为526.6mg/g。FTIR、XPS表征结果表明Me@SA/GA吸附U(VI)的相互作用包括静电吸引、颗粒内扩散以及水凝胶的官能团(羧基、氨基和羟基)与U(VI)的配位。Me@SA/GA投加量1g/L对某实际稀土废水试验,其出水U(VI)浓度为0.02mg/L,可达到我国稀土工业污染物排放标准(GB26451-2011)要求。