Ti/RuO2-CoO电极制备及其氨氮降解性能

采用热氧化法制备Ti/RuO_2-CoO电极,通过SEM和XRD对电极涂层的表面形貌和晶体结构进行表征;并利用最佳条件制备的电极开展电化学氧化氨氮模拟废水研究。实验研究了电流密度、初始pH值、Cl~-浓度和NH_3-N初始浓度对NH_3-N降解效果的影响。研究结果表明:当n(Ru)/n(Co)=7∶3时Ti/RuO_2-CoO电极对NH_3-N的去除效果较好。随着电流密度的增加,NH_3-N去除率随之升高;初始pH为碱性条件时,NH_3-N去除效果较好;NH_3-N去除率随Cl~-浓度的增加呈现先增大后减小,当Cl~-浓度为3 000 mg/L时,氨氮去除率达到97.95%。当电流密度为70 mA/cm~2、Cl~-浓度为3 000 mg/L、初始pH=9时,经过180 min电解后,氨氮初始浓度从500 mg/L降低至10.25 mg/L,且电化学氧化氨氮的产物主要为氮气和硝酸盐氮。     

改性Ti/SnO2-Sb电极降解硝基苯废水

采用热分解法制备了Ti/SnO2-Sb电极,并通过掺杂Cu,Ni,La,Ce,Nd,Zn和Bi等金属对该电极进行改性.采用扫描电子显微镜(SEM)及X射线衍射(XRD)等方法表征了电极的形貌及晶型;通过加速电极寿命测试和电催化降解硝基苯模拟废水实验,研究了金属掺杂对Ti/SnO2-Sb电极稳定性及电催化活性的影响.根据硝基苯降解的动力学方程分析不同金属掺杂对电极降解速率的影响;通过质谱对硝基苯的降解机理进行了初步探讨;采用水杨酸捕集羟基自由基的液相色谱法测定OH.的浓度.实验结果表明,与空白Ti/SnO2-Sb电极相比,金属掺杂改善了电极的表面形貌和SnO2衍射峰的强度,提高了Ti/SnO2-Sb阳极的电解寿命.对硝基苯模拟废水的电解实验结果表明,掺杂电极的电催化降解能力显著提高,硝基苯的降解符合准一级反应动力学方程.质谱分析结果表明,硝基苯在阴极被还原成苯胺并被氧化降解成其它有机物的过程发生迅速.羟基自由基浓度测定结果表明,自由基浓度越高,硝基苯降解速率越快,反应60 min时,空白Ti/SnO2-Sb电极的OH·浓度只有掺Cu金属电极的1/5.     

Ti/SnO2+Sb2O3/Fe-PbO2电极电催化性能研究

制备了Ti/SnO2+Sb2O3/Fe-PbO2阳极,采用SEM、XRD和ICP对电极的表面形貌和组成进行了表征.为了考察电极的电催化活性,以苯酚为目标污染物,进行了电催化降解实验.研究结果表明Ti/SnO2+Sb2O3/Fe-PbO2电极电催化降解苯酚模拟废水的最佳工艺条件为:电流密度10mA/cm2、支持电解质Na2SO4浓度0.05 mol/L、温度25℃.在25℃时苯酚的电催化氧化降解反应遵循一级反应动力学规律,并且苯酚的电催化氧化主要是·OH参与的间接氧化,反应过程中电极表面产生的羟基自由基对苯酚的氧化去除起着主要作用.     

Ti/α-PbO_2/β-PbO_2电极电化学降解2-氯酚（英文）

采用电化学沉积法在Ti基底上制备了复合电极Ti/α-PbO 2/β-PbO 2,扫描电镜结果表明电极呈现由β-PbO 2小晶体组成的菜花状微观形貌.所制电极在电化学降解环境污染物2-氯酚时表现出较高的电催化效率、较好的电极稳定性和较长的电极寿命.用正交实验优化了电化学降解2-氯酚的实验条件.在最优的实验条件(2-氯酚初始浓度50 mg/L,电解质0.1 mol/L Na2SO4,温度35 oC,阳极电流密度20 mA/cm2)下电化学降解180 min后,2-氯酚的去除率达100%.动力学结果表明,Ti/α-PbO 2/β-Pb O2电极上2-氯酚的电化学氧化符合准一级动力学过程.     

Ti/α-PbO2/β-PbO2电极电化学降解2-氯酚

采用电化学沉积法在Ti基底上制备了复合电极Ti/α-PbO2/β-PbO2,扫描电镜结果表明电极呈现由β-PbO2小晶体组成的菜花状微观形貌.所制电极在电化学降解环境污染物2-氯酚时表现出较高的电催化效率、较好的电极稳定性和较长的电极寿命.用正交实验优化了电化学降解2-氯酚的实验条件.在最优的实验条件(2-氯酚初始浓度50 mg/L,电解质0.1 mol/L Na2SO4,温度35oC,阳极电流密度20 mA/cm2)下电化学降解180 min后,2-氯酚的去除率达100%.动力学结果表明, Ti/α-PbO2/β-PbO2电极上2-氯酚的电化学氧化符合准一级动力学过程.     

Ti/Sb2O5-SnO2/PbO2电极电催化氧化对氨基苯酚

以电沉积法制备的Ti／Sb2O5-SnO2／PbO2电极作阳极,恒电流电解水溶液中的对氨基苯酚（PAP）,利用紫外光谱探讨了对氨基苯酚电催化氧化的反应历程,系统地考察了电解时间、反应温度,pH值、电流密度以及对氨基苯酚初始浓度对COD去除率的影响,提出了电催化氧化对氨基苯酚的最佳条件．结果表明,对氨基苯酚电催化反应为逐级氧化历程,主要中间产物为苯醌、丁烯二酸和草酸,最终产物为CO2和水．20℃,对初始浓度10mg／L的对氨基苯酚水溶液（pH=6）,恒定电流密度100mA／cm^2,电解1h,COD去除率可达98．5％．该方法作为废水中对氨基苯酚的最小化处理．具有良好的应用前景．     

Keggin型杂多阴离子PW11O39Fe(III)(H2O)4-电催化降解硝基苯

以Keggin型铁取代杂多阴离子PW11O39Fe(III)(H2O)4－ (PW11Fe)代替传统电芬顿(electro-Fenton)方法中的Fe3＋作为电催化剂, 构成一个新颖的电催化体系并用于中性水溶液中硝基苯的降解. 结果表明, 含有1.0 mmol•L－1硝基苯和1.0 mmol•L－1 PW11Fe的混合磷酸盐溶液(pH 6.86), 在－0.5 V电位和60 mL•min－1 O2流速下反应100 min, 硝基苯便完全降解. 降解的准一级表观速率常数与硝基苯的初始浓度有关, 当硝基苯的初始浓度为1.0, 2.0和5.0 mmol•L－1时, kobs分别为7.18×10－2, 3.57×10－2和1.47×10－2 min－1. 降解反应100 min的TOC(有机碳总量)去除率约为35%, 表明硝基苯的降解过程伴随着矿化.     

镧掺杂对Ti/Sb-SnO2阳极电催化性能影响的研究

元素掺杂是一种有效改善电极性能的手段。为了提高钛基锡系形稳阳极的催化活性,La被作为一种改性剂掺杂在Ti/Sb-SnO2电极的涂层中。掺杂改性后电极涂层的形貌通过SEM及XRD进行了检测;并通过EDS检测了涂层中各元素的组成比例;利用电化学阳极极化曲线(LSV)测试了电极的电化学性能。利用掺杂改性后的电极和未改性电极电解处理模拟对硝基苯酚(p-NP)废水,在相同条件下,掺杂La改性后电极处理废水的降解率为92.8%,远高于未改性电极处理废水的降解率(72%)。实验表明,稀土La改性后的Ti/Sb-SnO2电极在处理p-NP废水的优越性相当明显。     

三维电极系统电化学氧化三唑酮

以三唑酮(TDF)为目标污染物,以钛基钌铱电极和不锈钢板作阳极、阴极,颗粒活性炭(GAC)为粒子电极构建三维电极系统,通过搅拌实现粒子电极呈流化状态。研究电流密度、TDF初始浓度、GAC投加量、初始pH对三维电极系统的TDF去除效率的影响。研究结果表明:增大电流密度有助于提高TDF去除效率;TDF去除率随初始pH的增大呈现逐渐增大的趋势,碱性条件有助于TDF的去除;当GAC投加量为1～4 g/L时,增大GAC投加量有助于TDF的降解;增大TDF初始浓度会导致去除率的降低。当TDF初始浓度为200μg/L、电流密度为8m A/cm2、初始pH=11、GAC投加量为4 g/L时,电化学氧化10 min时TDF去除率达到99.95%。三维电极系统的传质效率高于二维电极系统,三维电极电化学氧化系统是一种适用于降解TDF的高级氧化技术。     

Fe2O3/TiO2纳米管的制备及其光电催化降解染料废水性能

采用阴极电沉积和阳极氧化法制备了Fe2O3改性TiO2纳米管(Fe2O3/TiO2-NTs)电极,运用场发射扫描电子显微镜、透射电子显微镜、X射线衍射和紫外-可见漫反射光谱等手段对其进行了表征,考察了其光电化学性能,并研究了复合电极光电催化降解甲基橙染料废水的反应性能.结果表明,Fe2O3的负载成功地将TiO2-NTs的光响应区间拓宽到可见光区域,Fe2O3/TiO2-NTs复合电极的光电流密度达到TiO2-NTs电极的3倍.在光电催化反应中,Fe2O3/TiO2-NTs复合电极对甲基橙的脱色效果明显优于TiO2-NTs电极,以Fe2O3/TiO2-NTs为阳极,光照5min,甲基橙溶液的脱色率可达90%以上.     

Microstructural impact of anodic coatings on the electrochemical chlorine evolution reaction

Sol-gel Ru(0.3)Sn(0.7)O(2) electrode coatings with crack-free and mud-crack surface morphology deposited onto a Ti-substrate are prepared for a comparative investigation of the microstructural effect on the electrochemical activity for Cl(2) production and the Cl(2) bubble evolution behaviour. For comparison, a state-of-the-art mud-crack commercial Ru(0.3)Ti(0.7)O(2) coating is used. The compact coating is potentially durable over a long term compared to the mud-crack coating due to the reduced penetration of the electrolyte. Ti L-edge X-ray absorption spectroscopy confirms that a TiO(x) interlayer is formed between the mud-crack Ru(0.3)Sn(0.7)O(2) coating and the underlying Ti-substrate due to the attack of the electrolyte. Meanwhile, the compact coating shows enhanced activity in comparison to the commercial coating, benefiting from the nanoparticle-nanoporosity architecture. The dependence of the overall electrode polarization behaviour on the local activity and the bubble evolution behaviour for the Ru(0.3)Sn(0.7)O(2) coatings with different surface microstructure are evaluated by means of scanning electrochemical microscopy and microscopic bubble imaging.     

Nanostructured Ti(0.7)Mo(0.3)O2 support enhances electron transfer to Pt: high-performance catalyst for oxygen reduction reaction

The slow rate of the oxygen reduction reaction (ORR) and the instability of Pt-based catalysts are two of the most important issues that must be solved in order to make proton exchange membrane fuel cells (PEMFCs) a reality. Additionally, the serious carbon corrosion on the cathode side is a critical problem with respect to the durability of catalyst that limits its wide application. Here, we present a new approach by exploring robust noncarbon Ti(0.7)Mo(0.3)O(2) used as a novel functionalized cocatalytic support for Pt. This approach is based on the novel nanostructure Ti(0.7)Mo(0.3)O(2) support with "electronic transfer mechanism" from Ti(0.7)Mo(0.3)O(2) to Pt that can modify the surface electronic structure of Pt, owing to a shift in the d-band center of the surface Pt atoms. Furthermore, another benefit of Ti(0.7)Mo(0.3)O(2) is the extremely high stability of Pt/Ti(0.7)Mo(0.3)O(2) during potential cycling, which is attributable to the strong metal/support interaction (SMSI) between Pt and Ti(0.7)Mo(0.3)O(2). This also enhances the inherent structural and chemical stability and the corrosion resistance of the TiO(2)-based oxide in acidic and oxidative environments. We also demonstrate that the ORR current densities generated using cocatalytic Pt/Ti(0.7)Mo(0.3)O(2) are respectively ~7- and 2.6-fold higher than those of commercial Pt/C and PtCo/C catalysts with the same Pt loading. This new approach opens a reliable path to the discovery advanced concept in designing new catalysts that can replace the traditional catalytic structure and motivate further research in the field.     

乙酰丙酮钌催化硝基苯氢转移氢化制苯胺

以自制的乙酰丙酮钌配合物（Ru(acac)3）为催化剂,甲酸钠为氢供体,十六烷基三甲基溴化铵为乳化剂,研究了水溶液中催化硝基苯氢转移氢化制苯胺的工艺。 确定了适宜反应条件为：甲酸钠和硝基苯摩尔比为2∶1,反应温度80 ℃,反应时间4.0 h,Ru(acac)3用量为硝基苯质量的4%。 硝基苯的转化率和苯胺产率分别为100%和96.65%,表明Ru(acac)3对硝基苯氢转移氢化制苯胺具有优异的催化作用。     

医院污水的电化学法消毒试验研究

应用电化学方法消毒处理医院污水,比较不同阳极材料消毒效果,并探讨消毒机理.试验表明,以涂有贵金属(钌、铂、铱)氧化物的钛板作阳极,不锈钢板作阴极,在电流密度6 mA/cm2、水力停留时间15 m in、空气流量为40 L/h、极水比为1.0的试验条件下,消毒后污水的总大肠菌群数<500CFU/L,达到国家一级排放标准(GB8978—1996).     

钌-钯掺杂Ti/TiO2阳极电催化降解甲基橙研究

以偶氮染料甲基橙为处理对象, 分别考察了Ru, Pd及Ru-Pd掺杂的Ti/TiO2阳极的光、电催化活性, 并与Ti/RuOx-PdO阳极的电催化活性进行了比较; 利用XPS分析了Ru-Pd掺杂的Ti/TiO2阳极表面Ru, Pd及Ti的化学形态. 实验发现, Ru, Pd及Ru-Pd掺杂的Ti/TiO2阳极的光催化活性都有所降低, 而其电催化活性却都有大幅提升, 特别是Ru-Pd掺杂的Ti/TiO2阳极, 其电催化活性明显地优于Ti/RuOx-PdO阳极. XPS分析表明, Ru-Pd掺杂的Ti/TiO2阳极其光、电催化活性的变化可能与该阳极表面Ru, Pd及Ti的化学形态变化有关.     

长寿命、高倍率(Li4Ti5O12-AC)/( LiMn2O4-AC)电池电容的制备及性能研究

以商业微米级锰酸锂(LiMn2O4)为正极,钛酸锂(Li4Ti5O12)为负极,分别与商业活性炭(AC)复合,组装成软包装电池电容样品并进行电化学测试。测试结果表明：当样品正负极均复合AC时,其电化学性能要优于只有正极复合AC和未复合AC的样品。其中,正负极活性炭复合比例为5 wt.%,负极与正极的理论容量比(N/P)为1.01时,电池电容样品拥有良好的倍率性能,且其在0.5 C时的放电比容量为56.4 mAh/g,5 C时的容量保持率为0.5 C的72.2%。此外,与未复合AC的样品相比,单体在5 C倍率下经2000次循环后的容量保持率仍有77.5%,远高于前者的30.4%。     

利用Nafion膜和SFCN在低温常压下电化学合成氨

用溶胶-凝胶法制备了Ce0.8Sm0.2O2δ（SDC）和SmFe0.7Cu0.3-xNixO3（x=0,0.1,0.2,0.3）（SFCN）系列超细粉体,用XRD、TEM和SEM等方法对其进行了表征.分别将NiO-SDC和SFCN系列超细粉体干压成片并烧结成陶瓷,以SFCN系列陶瓷片为阴极,Nafion膜为电解质,NiO-SDC还原后得到的Ni-SDC金属陶瓷为阳极,银-铂网为集流体组成单电池,在低温常压下研究了其在电化学合成氨中的性能.结果表明：在25-100℃和施加电压的条件下,使用SFCN系列陶瓷片为阴极时均有氨气在阴极生成,其中SmFe0.7Cu0.1Ni0.2O3作阴极时电化学合成氨的性能最佳,在80℃时氨的合成速率为1.13×10^-8mol·s^-1·cm^-2,其电流效率为90.4%.     

改性二氧化钛负载贵金属Ru催化剂催化降解苯胺溶液

苯胺类废水污染物具有结构复杂、浓度高、不易生物降解、生物毒性大等特点,传统的苯胺降解措施存在着许多弊端,很难达到排放标准.催化湿法氧化技术(CWAO)主要针对降解高浓度难降解的有机废水,表现出降解效率高、反应时间短、对生物毒性物质的废水降解效果良好等优点,越来越受到人们的重视.但催化剂在使用过程中,需要在高温高压下进行,且有机物降解产生了有机酸,使得催化剂的活性组分流失和载体的物理化学性质发生变化,导致其催化活性下降.因此,需要开发出一种降解活性高,性能稳定的催化剂成为此技术在工业中广泛应用的关键.本文采用溶胶凝胶法对二氧化钛进行改性,制备了Ti0.9Zr0.1O2和Ti0.9Ce0.1O2载体,采用过量浸渍法将三氯化钌负载到载体表面制备了2%Ru/Ti0.9Zr0.1O2和2%Ru/Ti0.9Ce0.1O2催化剂.在高温高压反应条件下,以苯胺为催化湿法氧化污染物,对不同催化剂湿法降解苯胺进行比较研究,系统地探究了催化降解的反应温度和反应压力对苯胺降解的影响.此外,利用HPLC-MS鉴定出催化降解产生的中间产物,确定了催化降解的反应路径图.在改性的催化剂中,2%Ru/Ti0.9Zr0.1O2催化剂表现出最高的催化降解活性和稳定性.在初始苯胺浓度4 g/L,催化剂浓度4 g/L,反应温度180℃,O2压力1.5 MPa下,反应时间5 h后,苯胺完全转化,COD转化率达88.3%.并且催化剂进行三次循环试验后,苯胺转化率仍接近100%.X射线衍射和N2物理吸附结果表明,Ce,Zr掺杂到TiO2晶格中形成了共溶体,其晶格尺寸更小,比表面积和孔体积更大.负载贵金属后,并未出现其他晶相,说明贵金属均匀分散在载体表面.透射电镜结果表明,贵金属负载在改性TiO2上表现出较好的分散性和较小的颗粒尺寸,为催化降解苯胺提供更多的催化活性位点,而Ru/TiO2催化剂表面,贵金属发生团聚现象且颗粒尺寸大.X射线光电子能谱结果表明,Ce,Zr的掺杂使得TiO2表面活性氧和四价Ru的含量增加,更多的表面活性氧成为催化降解苯胺的直接原因.H2程序升温还原结果表明,在300?400oC处还原峰对应于催化剂载体晶格氧的还原,改性后,其还原峰增至2倍,即使在贫氧环境下,改性催化剂可以及时从载体中释放晶格氧,为催化降解苯胺提供更多的活性氧.     

Stepwise oxidation of anilines by cis-[RuIV(bpy)2(py)(O)]2+

The net six-electron oxidation of aniline to nitrobenzene or azoxybenzene by cis-[Ru(IV)(bpy)(2)(py)(O)](2+) (bpy is 2,2'-bipyridine; py is pyridine) occurs in a series of discrete stages. In the first, initial two-electron oxidation is followed by competition between oxidative coupling with aniline to give 1,2-diphenylhydrazine and capture by H(2)O to give N-phenylhydroxylamine. The kinetics are first order in aniline and first order in Ru(IV) with k(25.1 degrees C, CH(3)CN) = (2.05 +/- 0.18) x 10(2) M(-1) s(-1) (DeltaH(++) = 5.0 +/- 0.7 kcal/mol; DeltaS(++) = -31 +/- 2 eu). On the basis of competition experiments, k(H)2(O)/k(D)2(O) kinetic isotope effects, and the results of an (18)O labeling study, it is concluded that the initial redox step probably involves proton-coupled two-electron transfer from aniline to cis-[Ru(IV)(bpy)(2)(py)(O)](2+) (Ru(IV)=O(2+)). The product is an intermediate nitrene (PhN) or a protonated nitrene (PhNH(+)) which is captured by water to give PhNHOH or aniline to give PhNHNHPh. In the following stages, PhNHOH, once formed, is rapidly oxidized by Ru(IV)=O(2+) to PhNO and PhNHNHPh to PhN=NPh. The rate laws for these reactions are first order in Ru(IV)=O(2+) and first order in reductant with k(14.4 degrees C, H(2)O/(CH(3))(2)CO) = (4.35 +/- 0.24) x 10(6) M(-1) s(-1) for PhNHOH and k(25.1 degrees C, CH(3)CN) = (1.79 +/- 0.14) x 10(4) M(-1) s(-1) for PhNHNHPh. In the final stages of the six-electron reactions, PhNO is oxidized to PhNO(2) and PhN=NPh to PhN(O)=NPh. The oxidation of PhNO is first order in PhNO and in Ru(IV)=O(2+) with k(25.1 degrees C, CH(3)CN) = 6.32 +/- 0.33 M(-1) s(-1) (DeltaH(++) = 4.6 +/- 0.8 kcal/mol; DeltaS(++) = -39 +/- 3 eu). The reaction occurs by O-atom transfer, as shown by an (18)O labeling study and by the appearance of a nitrobenzene-bound intermediate at low temperature.     

Electronic modification of the [Ru(II)(tpy)(bpy)(OH(2))](2+) scaffold: effects on catalytic water oxidation

The mechanistic details of the Ce(IV)-driven oxidation of water mediated by a series of structurally related catalysts formulated as [Ru(tpy)(L)(OH(2))](2+) [L = 2,2'-bipyridine (bpy), 1; 4,4'-dimethoxy-2,2'-bipyridine (bpy-OMe), 2; 4,4'-dicarboxy-2,2'-bipyridine (bpy-CO(2)H), 3; tpy = 2,2';6',2'-terpyridine] is reported. Cyclic voltammetry shows that each of these complexes undergo three successive (proton-coupled) electron-transfer reactions to generate the [Ru(V)(tpy)(L)O](3+) ([Ru(V)=O](3+)) motif; the relative positions of each of these redox couples reflects the nature of the electron-donating or withdrawing character of the substituents on the bpy ligands. The first two (proton-coupled) electron-transfer reaction steps (k(1) and k(2)) were determined by stopped-flow spectroscopic techniques to be faster for 3 than 1 and 2. The addition of one (or more) equivalents of the terminal electron-acceptor, (NH(4))(2)[Ce(NO(3))(6)] (CAN), to the [Ru(IV)(tpy)(L)O](2+) ([Ru(IV)=O](2+)) forms of each of the catalysts, however, leads to divergent reaction pathways. The addition of 1 eq of CAN to the [Ru(IV)=O](2+) form of 2 generates [Ru(V)=O](3+) (k(3) = 3.7 M(-1) s(-1)), which, in turn, undergoes slow O-O bond formation with the substrate (k(O-O) = 3 × 10(-5) s(-1)). The minimal (or negligible) thermodynamic driving force for the reaction between the [Ru(IV)=O](2+) form of 1 or 3 and 1 eq of CAN results in slow reactivity, but the rate-determining step is assigned as the liberation of dioxygen from the [Ru(IV)-OO](2+) level under catalytic conditions for each complex. Complex 2, however, passes through the [Ru(V)-OO](3+) level prior to the rapid loss of dioxygen. Evidence for a competing reaction pathway is provided for 3, where the [Ru(V)=O](3+) and [Ru(III)-OH](2+) redox levels can be generated by disproportionation of the [Ru(IV)=O](2+) form of the catalyst (k(d) = 1.2 M(-1) s(-1)). An auxiliary reaction pathway involving the abstraction of an O-atom from CAN is also implicated during catalysis. The variability of reactivity for 1-3, including the position of the RDS and potential for O-atom transfer from the terminal oxidant, is confirmed to be intimately sensitive to electron density at the metal site through extensive kinetic and isotopic labeling experiments. This study outlines the need to strike a balance between the reactivity of the [Ru═O](z) unit and the accessibility of higher redox levels in pursuit of robust and reactive water oxidation catalysts.