NaCl胁迫对甜高粱发芽期生理生化特性的影响

为筛选耐盐甜高粱材料,探讨NaCl胁迫对甜高粱发芽期生理生化特性的影响,研究了0、70、140、210 mmol.L-1NaCl胁迫对吉甜3、BJK156、甜132、凯勒、威利、考利、吉甜2、戴尔等8个甜高粱材料发芽率、发芽势、发芽指数、活力指数、芽长、根长、芽鲜质量、根鲜质量等8个指标盐害系数的影响,利用系统聚类分类法对甜高粱耐盐性进行聚类可分为3类：耐盐性最强的是甜132,耐盐性中等的是BJK156,耐盐性较敏感的是考利、吉甜3、吉甜2、戴尔、凯勒、威利。进一步研究了盐胁迫对甜高粱芽苗中丙二醛、可溶性蛋白含量及过氧化物酶（POD）、过氧化氢酶（CAT）、超氧化物歧化酶（SOD）活性的影响。结果得出：随着盐胁迫的加重丙二醛含量逐渐增加,可溶性蛋白含量逐渐减少。NaCl胁迫不同程度地提高了8个甜高粱材料POD、CAT、SOD活性,受3种NaCl质量浓度胁迫后8个甜高粱材料POD、CAT、SOD活性的变化趋势不同,这可能是它们耐盐差异的生理原因之一。另外,在3种NaCl浓度胁迫后甜132中的丙二醛增加量在8个材料中都是最低的,这与系统聚类分析得出甜132耐盐性最强的结论相吻合。研究认为丙二醛含量的变化可以作为筛选发芽期耐盐甜高粱品种的一个指标。     

钒（V）—4—（2—噻唑偶氮）间苯二酚分光光度法测定过氧化氢

本文研究了过氧化氢,钒(Ⅴ)和4-(2-噻唑偶氮)间苯二酚(TAR)形成三元络合物的条件及组成,其最大吸收波长为570nm,摩尔吸光系数为4.2×10~4,组成为V(Ⅴ):TAR:H_2O_2=1:1:1,在高氯酸介质中显色时,铬(Ⅵ)和铜(Ⅱ)干扰较严重,其他常见的无机离子和有机酸允许存在量较高。方法用于自来水中过氧化氢的回收试验和酸牛奶中过氧化氢剩余量的测定,结果均较满意。     

国内外液相过氧化氢的测定方法及其进展

介绍过氧化氢在纺织行业、化工行业、造纸工业、环保行业、电子行业、食品卫生行业及其他领域的应用概况,系统总结国内外过氧化氢的测定技术进展,着重分析常规滴定法、电化学法、分光光度法、化学发光法、荧光光度法、色谱法等6种过氧化氢的检测分析方法,比较了各种分析方法的优缺点,并指出电化学分析方法领域中研究消除干扰和提高重现性将继续是研究的重点;分光光度法由于方法简单,不需要复杂的设备,选择性较好,但是其测试灵敏度取决于所产生吸光物质的摩尔吸收系数,方法应用有限;化学发光法和荧光法,灵敏度高,可实现连续自动操作,尽管需要昂贵的设备,但其市场应用前景还相当不错。目前酶的利用也在一定程度上提高了其灵敏度和选择性,同时流动技术的发展大大提高了其测定速度,因此,化学发光法和荧光法测定过氧化氢含量仍是今后学者研究的重点之一,具有相当广阔的前景。     

苄基苯酚聚氧乙烯醚对斑马鱼中期毒性研究

该实验利用斑马鱼作为研究对象,分别暴露在暴过气的自来水中(对照组)和含苄基苯酚聚氧乙烯醚(polyoxyethylene benzylphenol ether,BP)浓度分别为2、1、0.5、0.25、0 mg/L水溶液(暴露组)中。暴露30 d后,将斑马鱼解剖收集肝脏,并分别对过氧化氢酶(CAT)、总谷胱甘肽(GSH)、丙二醛(MDA)、过氧化氢(H2O2)、超氧化物歧化酶(SOD)含量进行测定,并观察斑马鱼肝脏和性腺病理变化。结果表明:不同浓度的BP处理30 d后,浓度为0.025、0.05和0.1 mg/L组斑马鱼的过氧化氢酶活性显著高于对照组(p0.05);浓度为0.025、0.05、0.1和0.2 mg/L组斑马鱼总谷胱甘肽(T-GSH)含量显著低于对照组(p0.05);浓度为0.2 mg/L组斑马鱼抗氧化能力显著低于对照组(p0.05);丙二醛(MDA)含量各浓度组差异不显著。浓度为0.2 mg/L组斑马鱼超氧化物歧化酶显著高于对照组(p0.05);1和2 mg/L浓度处理组对肝细胞受到较为严重的损伤。而1和2 mg/L浓度组斑马鱼卵细胞发育速度明显较对照组加快,出现了大量的发育到晚期的初级卵母细胞。结果显示不同浓度BP对斑马鱼的氧化系统有不同程度的胁迫作用,高浓度组对斑马鱼的肝脏系统损伤较为严重,而对性腺细胞有促生长作用。     

大庆油田采油污水对斑马鱼过氧化氢酶的影响研究

为研究大庆油田采油污水对生物过氧化氢酶（Catalase,CAT）的毒性效应,判定采油污水对生物体的损害程度.以斑马鱼为实验材料,利用大庆油田不同稀释倍数（66.7倍、52.6倍、33.3倍）的采油污水胁迫培养斑马鱼,通过紫外分光光度法测定斑马鱼的不同部位CAT的变化情况,研究采油污水对斑马鱼毒性效应.结果表明,在相同的处理时间和环境条件下,随着采油污水稀释倍数的减小,斑马鱼的不同部位的CAT含量呈增加趋势,当达到一定稀释倍数时CAT的增长发生抑制,CAT含量减少,斑马鱼的生理状况也随之产生变化,甚至死亡.为此需要重视对大庆油田采油污水排放的监管、规范和治理.     

硅基载铁材料催化H_2O_2降解染料废水

采用浸渍-高温煅烧的方法制备了负载型Fe/Si O2催化材料,并利用该催化材料催化H_2O_2降解亚甲基蓝废水,同时考查了不同因素对亚甲基蓝降解效果的影响。结果表明,催化材料催化H_2O_2对亚甲基蓝废水具有较好的去除效果,受到催化材料投加量、H_2O_2浓度、pH、反应时间等因素影响。正交试验结果表明,影响因素的主次关系依次为H_2O_2浓度、pH值、反应时间及催化材料的投加量。为了考查该催化材料稳定性,经4次循环利用后,发现亚甲基蓝脱色率仍在97%以上。此外,该催化材料催化H_2O_2降解工业染料废水,色度去除率达到近100%,并且其COD去除率达到84.3%,符合染料废水达标排放要求。     

生物降解型消油剂与180#燃料油对黄海胆（Glyptocidaris crenularis）CAT和SOD活性的影响

为研究消油剂和溢油对海洋底栖生物的急性毒性效应,将黄海胆（Glyptocidaris crenularis）暴露于不同浓度（油水配比浓度分别为0.92 g/L、1.84 g/L、3.68 g/L）的180#燃料油分散液（water-accommodated fractions,WAFs）和经生物降解型消油剂处理后得到的乳化液（Biological enhanced water-accommodated fractions,BEWAFs）中,分别于暴露期24 h、48 h和96 h及恢复期24 h和48 h时,检测WAFs和BEWAFs对海胆性腺和肠组织的过氧化氢酶（CAT）和超氧化物歧化酶（SOD）的影响。结果显示,暴露在WAFs和BEWAFs中的性腺组织CAT、SOD和肠组织CAT活性总体呈先升高后降低趋势,而肠组织SOD活性随着暴露时间的增加呈升高—降低—升高趋势。肠组织中两种酶活性的最大诱导值出现的时间早于性腺组织,且恢复期时肠组织中各浓度组与对照组间差异更为显著,说明肠组织受石油烃氧化胁迫的敏感性比性腺组织强。与WAFs和BEWAFs相比,消油剂对照组中两种酶活性变化较小,由此可知,生物降解型消油剂本身对黄海胆的影响非常小,但其与燃料油对黄海胆的复合毒性效应却大于燃料油本身。海胆体内的CAT和SOD活性对石油烃的急性毒性效应较为敏感,可作为监测海上石油烃污染程度的生物标志物。     

Effects of free iron oxyhydrates and soil organic matter on copper sorption-desorption behavior by size fractions of aggregates from two paddy soils

Effects of free iron oxyhydrates (Fed) and soil organic matter (SOM) on copper (Cu2+) sorption-desorption behavior by size fractions of aggregates from two typical paddy soils (Ferric-Accumulic Stagnic Anthrosol (Soil H) and Gleyic Stagnic Anthrosol (Soil W)) were investigated with and without treatment of dithionite-citrate-bicarbonate and of H2O2. The size fractions of aggregates were obtained from the undisturbed bulk topsoil using a low energy ultrasonic dispersion procedure. Experiments of equilibrium sorption and subsequent desorption were conducted at soil water ratio of 1:20, 25℃. For Soil H, Cu2+ sorption capacity of the DCB-treated size fractions was decreased by 5.9% for fine sand fraction, by 40.4% for coarse sand fraction, in comparison to 2.9% for the bulk sample. However, Cu2+ sorption capacities of the H2O2-treated fractions were decreased by over 80% for the coarse sand fraction and by 15% for the clay-sized fraction in comparison to 88% for bulk soil. For Soil W, Cu2+ sorption capacity of the DCB-treated size fraction was decreased by 30% for the coarse sand fraction and by over 75% for silt sand fraction in comparison to 44.5% for the bulk sample. Cu2+ sorption capacities of the H2O2-treated fractions were decreased by only 2.0% for the coarse sand fraction and by 15% for the fine sand fraction in comparison to by 3.4% for bulk soil. However, Cu2+ desorption rates were increased much in H2O2-treated samples by over 80% except the clay-sized fraction (only 9.5%) for Soil H. While removal of SOM with H2O2 tendend to increase desorption rate, DCB- and H2O2-treatments caused decrease in Cu2+ retention capacity of size fractions. Particularly, there hardly remained Cu2+ retention capacity by size fractions from Soil H after H2O2 treatment except for clay-sized fraction. These findings supported again the dominance of the coarse sand fraction in sorption of metals and the preference of absorbed metals bound to SOM in differently stabilized status among the size fractions. Thus, enrichment and turnover of SOM in paddy soils may have great effects on metal retention and chemical mobility in paddy soils.     

Optimizing aerobic biodegradation of dichloromethane using response surface methodology

Response surface methodology (RSM) was employed to evaluate the optimum aerobic biodegradation of dichloromethane (DCM) in pure culture. The parameters investigated include the initial DCM concentration, glucose as an inducer and hydrogen peroxide as terminal electron acceptor (TEA). Maximum aerobic biodegradation efficiency was predicted to occur when the initial DCM concentration was 380 mg/L, glucose 13.72 mg/L, and H2O2 115 mg/L. Under these conditions the aerobic biodegradation rate reached up to 93.18%, which was significantly higher than that obtained under original conditions. Without addition of glucose, degradation efficiencies were 6 80% at DCM concentrations < 326 mg/L. When concentrations of DCM were more than 480 mg/L, the addition of hydrogen peroxide did not help to significantly increase DCM degradation efficiency. When DCM concentrations increased from 240 to 480 mg/L, the overall DCM degradation efficiency decreased from 91% to 60% in the presence of H2O2 for 120 mg/L.