WO2022073350A1 - 一种基于磁性氧化石墨烯催化粒子电极三维电芬顿降解水中抗病毒药物残留的方法 - Google Patents

一种基于磁性氧化石墨烯催化粒子电极三维电芬顿降解水中抗病毒药物残留的方法 Download PDF

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WO2022073350A1
WO2022073350A1 PCT/CN2021/096173 CN2021096173W WO2022073350A1 WO 2022073350 A1 WO2022073350 A1 WO 2022073350A1 CN 2021096173 W CN2021096173 W CN 2021096173W WO 2022073350 A1 WO2022073350 A1 WO 2022073350A1
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graphene oxide
catalytic particle
fenton
antiviral drug
magnetic graphene
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PCT/CN2021/096173
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English (en)
French (fr)
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郭鹏然
蔡楠
白格
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广东省科学院测试分析研究所(中国广州分析测试中心)
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Publication of WO2022073350A1 publication Critical patent/WO2022073350A1/zh

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    • C—CHEMISTRY; METALLURGY
    • C02—TREATMENT OF WATER, WASTE WATER, SEWAGE, OR SLUDGE
    • C02F—TREATMENT OF WATER, WASTE WATER, SEWAGE, OR SLUDGE
    • C02F1/00—Treatment of water, waste water, or sewage
    • C02F1/46—Treatment of water, waste water, or sewage by electrochemical methods
    • C02F1/461—Treatment of water, waste water, or sewage by electrochemical methods by electrolysis
    • C02F1/46104—Devices therefor; Their operating or servicing
    • C02F1/46109—Electrodes
    • C02F1/46114—Electrodes in particulate form or with conductive and/or non conductive particles between them
    • C—CHEMISTRY; METALLURGY
    • C02—TREATMENT OF WATER, WASTE WATER, SEWAGE, OR SLUDGE
    • C02F—TREATMENT OF WATER, WASTE WATER, SEWAGE, OR SLUDGE
    • C02F1/00—Treatment of water, waste water, or sewage
    • C02F1/46—Treatment of water, waste water, or sewage by electrochemical methods
    • C02F1/461—Treatment of water, waste water, or sewage by electrochemical methods by electrolysis
    • C02F1/467—Treatment of water, waste water, or sewage by electrochemical methods by electrolysis by electrochemical disinfection; by electrooxydation or by electroreduction
    • C02F1/4672—Treatment of water, waste water, or sewage by electrochemical methods by electrolysis by electrochemical disinfection; by electrooxydation or by electroreduction by electrooxydation
    • C—CHEMISTRY; METALLURGY
    • C02—TREATMENT OF WATER, WASTE WATER, SEWAGE, OR SLUDGE
    • C02F—TREATMENT OF WATER, WASTE WATER, SEWAGE, OR SLUDGE
    • C02F1/00—Treatment of water, waste water, or sewage
    • C02F1/72—Treatment of water, waste water, or sewage by oxidation
    • C02F1/725—Treatment of water, waste water, or sewage by oxidation by catalytic oxidation
    • C—CHEMISTRY; METALLURGY
    • C02—TREATMENT OF WATER, WASTE WATER, SEWAGE, OR SLUDGE
    • C02F—TREATMENT OF WATER, WASTE WATER, SEWAGE, OR SLUDGE
    • C02F2101/00—Nature of the contaminant
    • C02F2101/30—Organic compounds
    • C—CHEMISTRY; METALLURGY
    • C02—TREATMENT OF WATER, WASTE WATER, SEWAGE, OR SLUDGE
    • C02F—TREATMENT OF WATER, WASTE WATER, SEWAGE, OR SLUDGE
    • C02F2201/00—Apparatus for treatment of water, waste water or sewage
    • C02F2201/46—Apparatus for electrochemical processes
    • C02F2201/461—Electrolysis apparatus
    • C02F2201/46105—Details relating to the electrolytic devices
    • C02F2201/4612—Controlling or monitoring
    • C02F2201/46125—Electrical variables
    • C02F2201/46135—Voltage
    • C—CHEMISTRY; METALLURGY
    • C02—TREATMENT OF WATER, WASTE WATER, SEWAGE, OR SLUDGE
    • C02F—TREATMENT OF WATER, WASTE WATER, SEWAGE, OR SLUDGE
    • C02F2303/00—Specific treatment goals
    • C02F2303/14—Maintenance of water treatment installations

Definitions

  • the invention relates to a method for degrading antiviral drug residues in water based on three-dimensional electro-Fenton of magnetic graphene oxide catalytic particle electrodes.
  • Antiviral drugs are widely used in the treatment of influenza, herpes, hepatitis and AIDS and other diseases. Since they cannot be completely absorbed and metabolized by the human body, they will be excreted into the environmental water body with human feces and urine. Residues of antiviral drugs in water are usually present in trace concentrations, but are highly toxic to biological populations in the water. Such pollutants generally have low biodegradability, and the current sewage treatment system with biological treatment as the core process cannot effectively remove them. In the past ten years, in order to prevent the outbreak of epidemics and treat viral infections, antiviral drugs have been widely used. Their continuous discharge into environmental water bodies can cause changes in potential ecosystems, spawn drug-resistant strains, and seriously threaten aquatic life and environmental safety. Increase the risk of developing drug resistance in humans.
  • the commonly used treatment methods include physical methods, biological methods and chemical methods.
  • the physical method realizes the separation and enrichment of pollutants from the water phase through porous adsorption materials such as carbon and clay and membrane separation technology, but it cannot completely remove and degrade pollutants, and it is easy to cause secondary pollution.
  • the biological method realizes the metabolic transformation of antiviral drugs in the water environment through aerobic and anaerobic microbial treatment, but most drugs have a strong inhibitory effect on microorganisms and lead to bacterial species poisoning, resulting in low treatment efficiency.
  • AOPs advanced oxidation methods
  • Electro-Fenton is one of the most promising AOPs technologies, and has the advantages of simple equipment, mild operating conditions, and easy automatic control. It can efficiently generate OH to decompose organic pollutants quickly and thoroughly.
  • Three-dimensional electro-Fenton is the addition of particle electrodes to the reaction cell of a two-dimensional electrochemical reactor, which are polarized into tiny electrolytic cells under the action of an electric field, which increases the active electrode area and promotes surface mass transfer, thereby improving degradation efficiency.
  • the existing particle electrodes are still insufficient in terms of corrosion resistance, catalytic activity, stability and reusability, which limit the application of three-dimensional electro-Fenton technology in practical sewage treatment.
  • the object of the present invention is to provide a method for degrading antiviral drug residues in water based on three-dimensional electro-Fenton of magnetic graphene oxide catalytic particle electrodes, which has high degradation efficiency, simple process, wide pH range of applicable water quality, strong corrosion resistance, magnetic graphite oxide
  • the ene catalytic particle electrode is easy to recycle and can be reused.
  • a method for three-dimensional electro-Fenton degradation of antiviral drug residues in water based on magnetic graphene oxide catalytic particle electrodes comprises the following steps: adding 0.005-0.08 mol/L Na 2 SO 4 electrolyte solution in a three-dimensional electro-Fenton reaction vessel , Magnetic graphene oxide catalytic particle electrodes and water containing antiviral drug residues, the dosage of catalytic particle electrodes in the three-dimensional electric Fenton reactor is 5-45g/L, and the concentration of antiviral drugs in the water containing antiviral drug residues 15-25mg/L, adjust the electrode plate spacing to 2-6cm, the applied voltage to 5-30V, control the initial pH value of the three-dimensional electro-Fenton electrolytic cell to be 3-11, turn on aeration, and the aeration intensity is 0.4-12L /min, to degrade antiviral drug residues in water; the preparation method of the magnetic graphene oxide catalytic particle electrode comprises the following steps:
  • Step S1 Weigh montmorillonite (MMT) and single-layer graphene oxide (GO) powder in a beaker, the mass ratio of montmorillonite and single-layer graphene oxide powder is 3: (1 ⁇ 1.5), add ethylene glycol alcohol, after ultrasonication, a brownish-yellow homogeneous suspension is formed;
  • MMT montmorillonite
  • GO single-layer graphene oxide
  • Step S2 Weigh FeCl 3 ⁇ 6H 2 O, anhydrous sodium acetate, polyethylene glycol in a beaker, and the mass ratio of FeCl 3 ⁇ 6H 2 O, anhydrous sodium acetate and polyethylene glycol is 1: (3.5 ⁇ 3.8): (1.8 ⁇ 2.2), add ethylene glycol for simple mixing, then add to the suspension obtained in step S1, stir, and put the stirred solution into a polytetrafluoroethylene autoclave for heating, and the heating temperature is 150 ⁇ 250°C, the heating time is 7 ⁇ 9h, the obtained black solid is washed several times with ethanol, dried in a vacuum drying box at 45 ⁇ 55°C for 7.5 ⁇ 8.5h, then ground with a mortar, and passed through a 80 ⁇ 120 mesh sieve to obtain black powder;
  • Step S3. Mix the black powder with the 4wt% polyvinyl alcohol aqueous solution, the mass ratio of the black powder to the 4wt% polyvinyl alcohol aqueous solution is (2-2.5): 1, and use a sliver to extrude long strips with a diameter of 5-7 mm, Place it on a ball rolling board for granulation to obtain round granules with a diameter of 5-7 mm; freeze-dry the round granules, and calcine at 550-650 °C for 100-150 min under a N 2 protective atmosphere, and finally obtain a diameter of 4.8-5.5 mm of magnetic graphene oxide catalytic particle electrode, denoted as magnetic MMT/GO/ Fe3O4 catalytic particle electrode .
  • step S1 the volume of ethylene glycol added is 45-55ml, and the ultrasonic time is 55-65min.
  • step S2 the volume of ethylene glycol added is 20-30ml, and the stirring time is 55-65min.
  • the antiviral drugs include acyclovir and arbidol.
  • the antiviral drug is acyclovir
  • 20 mg/L of humic acid is also added to the system, which has a better degradation effect due to the synergistic promotion effect.
  • the present invention can efficiently degrade target pollutants, and the removal rate of antiviral drugs is significantly higher than that of traditional two-dimensional electrodes, three-dimensional electrodes and electro-Fenton advanced oxidation technologies, and the removal rate of antiviral drugs is improved compared with three-dimensional electrode technology. Compared with the electro-Fenton technology, the removal rate of antiviral drugs is increased by 12%.
  • the present invention is suitable for a wide pH range of water quality, and has little requirement for the actual pH of the water body. In the range of pH 3 to 11, the removal rate of antiviral drugs can be maintained at more than 85%, which greatly improves the dependence of the electro-Fenton system. The problem with acidic pH.
  • the preparation method of the magnetic graphene oxide catalytic particle electrode is simple in this application.
  • the montmorillonite is used as a carrier, combined with graphene oxide, and loaded with Fe 3 O 4 nanoparticles, which expands the lamellar spacing of montmorillonite and increases
  • the adsorption site and specific surface area of the catalytic particle electrode improve the adsorption ability and electrocatalytic ability of the antiviral drug of the magnetic graphene oxide catalytic particle electrode.
  • the magnetic graphene oxide-based catalytic particle electrode has high recycling rate, strong stability, and is easy to be separated from water due to its magnetic properties.
  • the removal rate of antiviral drugs by electro-Fenton technology can be maintained above 90%.
  • the present application has the advantages of short-term high efficiency, high degradation efficiency, simple process, wide pH range of applicable water quality, strong corrosion resistance, easy recovery of the magnetic graphene oxide catalytic particle electrode, reusability, high reuse rate and strong stability.
  • Fig. 1 is the magnetic MMT/GO/Fe 3 O 4 particle electrode scanning electron microscope (SEM) image obtained in Example 1;
  • Fig. 2 is the variation curve of acyclovir degradation with time in Example 1;
  • Figure 3 is a comparison of the effect of different electrochemical advanced oxidation technologies for degrading acyclovir, among which, 2D: two-dimensional electrode; 3D: three-dimensional electrode; EF: electro-Fenton; 3D-EF: magnetic graphene oxide catalytic particle-based electrode 3D Electro-Fenton Technology.
  • montmorillonite As the carrier, graphene oxide was used to open the layered structure, and Fe 3 O 4 nanoparticles were supported, and the magnetic MMT/rGO/Fe 3 O 4 catalytic particle electrode was prepared by the method of hydrothermal-granulation-calcination. Weigh 0.3 g of montmorillonite MMT and 0.1 g of single-layer graphene oxide powder GO into a beaker, add 50 ml of ethylene glycol, and sonicate for 60 min to form a brownish-yellow uniform suspension.
  • Example 1 other parameters remained unchanged, and the initial pH of the reaction tank was controlled to be 3.0. After the reaction was completed, high-performance liquid chromatography was used for detection, and the degradation rate of acyclovir was 90%.
  • Example 1 other parameters remained unchanged, and the initial pH of the reaction tank was controlled to be 7.0. After the reaction was completed, high-performance liquid chromatography was used for detection, and the degradation rate of acyclovir was 96%.
  • Example 1 other parameters remained unchanged, and the initial pH of the reaction tank was controlled to be 9.0. After the reaction was completed, high-performance liquid chromatography was used for detection, and the degradation rate of acyclovir was 96%.
  • Example 1 other parameters remained unchanged, and the initial pH of the reaction tank was controlled to be 11.0. After the reaction was completed, high-performance liquid chromatography was used for detection, and the degradation rate of acyclovir was 88%.
  • Example 1 the dosage of the magnetic graphene oxide catalytic particle electrode was 40 g/L, and after the reaction was completed, high-performance liquid chromatography was used to detect, and the degradation rate of acyclovir was 95%.
  • Example 1 the dosage of the magnetic graphene oxide catalytic particle electrode was 20 g/L, and after the reaction was completed, high performance liquid chromatography was used to detect, and the degradation rate to acyclovir was 93%.
  • Example 1 other parameters remained unchanged, and 20 mg/L of humic acid was also added. After the reaction was completed, high-performance liquid chromatography was used for detection, and the degradation rate of acyclovir was 91%.
  • Example 1 other parameters remained unchanged, the applied voltage was 20V, and after the reaction was completed, high performance liquid chromatography was used for detection, and the degradation rate of acyclovir was 94%.
  • Example 1 other parameters remained unchanged, the applied voltage was 30V, and after the reaction was completed, high performance liquid chromatography was used for detection, and the degradation rate of acyclovir was 93%.
  • Example 13 other parameters remain unchanged.
  • the magnetic graphene oxide catalytic particle electrode is separated and dried and reused. After ten cycles of use, the removal rate of acyclovir is still 92%.
  • the method for three-dimensional electro-Fenton degradation of antiviral drug residues in water based on magnetic graphene oxide catalytic particle electrodes has different initial pH and water quality conditions containing natural organic matter. Viral drugs have high degradation rates.
  • the method has a wide range of application, short treatment time, reusable catalyst, and high engineering application value.

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Abstract

一种基于磁性氧化石墨烯催化粒子电极三维电芬顿降解水中抗病毒药物残留的方法，该方法包括以下步骤：在三维电芬顿反应容器中，加入Na 2SO 4电解质溶液、磁性氧化石墨烯催化粒子电极和含抗病毒药物残留的水，三维电芬顿反应器中催化粒子电极的投加量为5～45g/L，含抗病毒药物残留的水中抗病毒药物的浓度为15～25mg/L，调节电极板间距为2-6cm，施加电压为5～30V，控制三维电芬顿电解池的初始pH值为3～11，开启曝气，对水中抗病毒药物残留降解。该方法降解效率高、工艺简单、适用水质pH范围广、耐腐蚀性强、磁性氧化石墨烯催化粒子电极易于回收，可重复利用。

Description

一种基于磁性氧化石墨烯催化粒子电极三维电芬顿降解水中抗病毒药物残留的方法 技术领域：
本发明涉及一种基于磁性氧化石墨烯催化粒子电极三维电芬顿降解水中抗病毒药物残留的方法。
背景技术：
抗病毒药物被广泛应用于治疗流感、疱疹、肝炎以及艾滋等疾病，由于人体服用后无法完全被吸收和代谢，它们会随人类的粪便和尿液排出体外进入到环境水体。抗病毒药物在水体中的残留通常以痕量浓度存在，但对水中的生物种群具有高毒性。这类污染物一般具有较低的生物降解性，目前以生物处理为核心工艺的污水处理系统无法有效去除。过去十年，为了预防流行病的爆发、治疗病毒感染，抗病毒药物大量使用，它们在环境水体中的持续排放可引起潜在生态系统的改变，催生抗药菌株，严重威胁水生生物和环境安全，加剧人类产生耐药性的风险。
对于水中抗病毒药物的去除，常用的处理手段包括物理法、生物法和化学法。物理法通过碳、粘土等多孔吸附材料及膜分离技术实现污染物从水相中的分离和富集，但无法实现污染物的彻底去除和降解，且易造成二次污染。生物法通过好氧、厌氧微生物处理实现抗病毒药物在水环境中的代谢转化，但大多数药物对微生物具有很强的抑制作用而导致菌种中毒，从而造成处理效率不高。化学法中最常用的技术之一是高级氧化法(AOPs)，它可以高效地将水中污染物降解为二氧化碳和水，并且避免产生二次污染。电芬顿是最有前景的AOPs技术之一，并具有设备简单、操作条件温和、易于实现自动控制的优势，可高效产生·OH快速彻底地分解有机污染物。三维电芬顿是在二维电化学反应器的反应池中加入粒子电极，它们 在电场的作用下极化为一个个微小的电解池，增加了活性电极面积，促进了表面传质，从而提高降解效率。但现有的粒子电极在抗腐蚀性、催化活性以及稳定性和重复利用性方面仍有不足，限制了三维电芬顿技术在实际污水处理中的应用。
发明内容：
本发明的目的是提供一种基于磁性氧化石墨烯催化粒子电极三维电芬顿降解水中抗病毒药物残留的方法，降解效率高、工艺简单、适用水质pH范围广、耐腐蚀性强、磁性氧化石墨烯催化粒子电极易于回收，可重复利用。
本发明是通过以下技术方案予以实现的：
一种基于磁性氧化石墨烯催化粒子电极三维电芬顿降解水中抗病毒药物残留的方法，该方法包括以下步骤：在三维电芬顿反应容器中，加入0.005～0.08mol/LNa 2SO 4电解质溶液、磁性氧化石墨烯催化粒子电极和含抗病毒药物残留的水，三维电芬顿反应器中催化粒子电极的投加量为5～45g/L，含抗病毒药物残留的水中抗病毒药物的浓度为15～25mg/L，调节电极板间距为2-6cm，施加电压为5～30V，控制三维电芬顿电解池的初始pH值为3～11，开启曝气，曝气强度为0.4～12L/min，对水中抗病毒药物残留降解；所述磁性氧化石墨烯催化粒子电极的制备方法包括以下步骤：
步骤S1.称取蒙脱土(MMT)和单层氧化石墨烯(GO)粉末于烧杯中，蒙脱土和单层氧化石墨烯粉末的质量比为3：(1～1.5)，加入乙二醇，经过超声后形成棕黄色的均匀悬浊液；
步骤S2.称取FeCl 3·6H 2O、无水乙酸钠、聚乙二醇于烧杯中，FeCl 3·6H 2O、无水乙酸钠和聚乙二醇的质量比为1：(3.5～3.8)：(1.8～2.2)，加入乙二醇进行简单混合，然后加入 步骤S1得到的悬浊液中，搅拌，将搅拌均匀的溶液放入聚四氟乙烯高压反应釜中加热，加热温度为150～250℃，加热时间为7～9h，得到黑色固体先用乙醇洗涤多次，在真空干燥箱中45～55℃干燥7.5～8.5h后使用研钵研磨，过80～120目筛后得到黑色粉末；
步骤S3.将黑色粉末与4wt％聚乙烯醇水溶液混合，黑色粉末与4wt％聚乙烯醇水溶液的质量比为(2～2.5)：1，使用出条器挤出直径为5～7mm长条，放置于搓丸板上进行造粒，得到直径为5～7mm圆形颗粒；将圆形颗粒冷冻干燥，并在N 2保护气氛下550～650℃煅烧100～150min，最终得到直径为4.8～5.5mm的磁性氧化石墨烯催化粒子电极，记为磁性MMT/GO/Fe 3O 4催化粒子电极。
其中，步骤S1，加入乙二醇的体积为45～55ml，超声时间为55～65min。
其中，步骤S2，加入乙二醇的体积为20～30ml，搅拌的时间为55～65min。
所述抗病毒药物包括阿昔洛韦、阿比朵尔。
当抗病毒药物为阿昔洛韦，优选地，体系中还加入20mg/L的腐殖酸，由于协同促进作用具有更好的降解效果。
本发明的有益效果如下：
1、本发明可高效降解目标污染物，对抗病毒药物的去除率明显高于传统的二维电极、三维电极和电芬顿高级氧化技术，相比于三维电极技术降解抗病毒药物去除率提高了40％，相比于电芬顿技术降解抗病毒药物去除率提高了12％。
2、本发明适用水质的pH范围广，对实际水体pH要求小，在pH 3～11的范围内，对抗病毒药物的去除率可保持在85％以上，极大地改善了电芬顿体系中依赖酸性pH的问题。
3、本申请基于磁性氧化石墨烯催化粒子电极的制备方法简单，以蒙脱土为载体，结合氧 化石墨烯，并负载Fe 3O 4纳米颗粒，扩大了蒙脱土的片层间距，增加了催化粒子电极的吸附位点和比表面积，从而提高了磁性氧化石墨烯催化粒子电极对抗病毒药物的吸附能力和电催化能力。
4、所述基于磁性氧化石墨烯催化粒子电极，重复利用率高，稳定性强，因具有磁性而易于从水体中分离，所述基于磁性氧化石墨烯催化粒子电极经十次循环使用，通过三维电芬顿技术对抗病毒药物的去除率可保持在90％以上。
总之，本申请短时高效，降解效率高、工艺简单、适用水质pH范围广、耐腐蚀性强、磁性氧化石墨烯催化粒子电极易于回收，可重复利用，重复利用率高，稳定性强。
附图说明：
图1是实施例1得到的磁性MMT/GO/Fe 3O 4粒子电极扫描电镜(SEM)图；
图2是实施例1阿昔洛韦降解随时间的变化曲线；
图3是不同电化学高级氧化技术降解阿昔洛韦的效果对比，其中，2D：二维电极；3D：三维电极；EF：电芬顿；3D-EF：基于磁性氧化石墨烯催化粒子电极的三维电芬顿技术。
具体实施方式：
以下是对本发明的进一步说明，而不是对本发明的限制。
实施例1：
以蒙脱土为载体，利用氧化石墨烯打开层状结构，并负载Fe 3O 4纳米颗粒，采用水热-造粒-煅烧的方法制备磁性MMT/rGO/Fe 3O 4催化粒子电极。称取0.3g蒙脱土MMT和0.1g单层氧化石墨烯粉末GO于烧杯中，加入50ml乙二醇，超声60min，形成棕黄色的均匀悬浊液。称取1.0gFeCl 3·6H 2O、3.6g无水乙酸钠，2.0g聚乙二醇于烧杯中，加入25ml乙二醇进 行简单混合，然后加入悬浊液中，放入磁子，于磁力搅拌器上搅拌60min。将搅拌均匀的溶液放入聚四氟乙烯高压反应釜中，于200℃下加热8小时，所得的黑色固体用乙醇洗涤3次，在真空干燥箱中50℃下干燥约8小时，使用研钵研磨，并过100目筛，得到黑色粉末。将黑色粉末与4wt％聚乙烯醇水溶液以2:1的质量比进行混合，使用出条器挤出直径为6mm的长条，放置于搓丸板上进行造粒，得到直径大约为6mm的圆形颗粒。将圆形颗粒冷冻干燥，并在N 2保护气氛下650℃煅烧120min，最终得到直径大约为5mm的磁性MMT/GO/Fe 3O 4催化粒子电极。
在反应容器中加入100mL浓度为20mg/L的抗病毒药物阿昔洛韦溶液，电极板间隔6cm,电解质Na 2SO 4投加量为0.02mol/L，曝气强度为2L/min，施加电压为10V，保持反应池原始pH为6.3和正常光照，粒子电极投加量为10g/L，降解时间120min。反应结束后，采用高效液相色谱进行检测，对阿昔洛韦的降解率为88％。
实施例2
参考实施例1，其他参数不变，控制反应池初始pH为3.0，反应结束后，采用高效液相色谱进行检测，对阿昔洛韦的降解率为90％。
实施例3
参考实施例1，其他参数不变，控制反应池初始pH为7.0，反应结束后，采用高效液相色谱进行检测，对阿昔洛韦的降解率为96％。
实施例4
参考实施例1，其他参数不变，控制反应池初始pH为9.0，反应结束后，采用高效液相色谱进行检测，对阿昔洛韦的降解率为96％。
实施例5
参考实施例1，其他参数不变，控制反应池初始pH为11.0，反应结束后，采用高效液相色谱进行检测，对阿昔洛韦的降解率为88％。
实施例6
参考实施例1，其他参数不变，磁性氧化石墨烯催化粒子电极投加量为40g/L，反应结束后，采用高效液相色谱进行检测，对阿昔洛韦的降解率为95％。
实施例7
参考实施例1，其他参数不变，磁性氧化石墨烯催化粒子电极投加量为20g/L，反应结束后，采用高效液相色谱进行检测，对阿昔洛韦的降解率为93％。
实施例8
参考实施例1，其他参数不变，降解时间90min，反应结束后，采用高效液相色谱进行检测，对阿昔洛韦的降解率为81％。
实施例9
参考实施例1，其他参数不变，还加入20mg/L的腐殖酸，反应结束后，采用高效液相色谱进行检测，对阿昔洛韦的降解率为91％。
实施例10
参考实施例1，其他参数不变，在反应容器中加入100mL浓度为20mg/L的抗病毒药物阿比朵尔溶液，降解时间15min。反应结束后，采用高效液相色谱进行检测，对阿比朵尔的降解率为96％。
实施例11
参考实施例1，其他参数不变，施加电压为20V，反应结束后，采用高效液相色谱进行检测，对阿昔洛韦的降解率为94％。
实施例12
参考实施例1，其他参数不变，施加电压为30V，反应结束后，采用高效液相色谱进行检测，对阿昔洛韦的降解率为93％。
实施例13
参考实施例1，其他参数不变，施加电压为20V，电极板间隔2cm，曝气强度为4L/min，粒子电极投加量为40g/L，反应结束后，采用高效液相色谱进行检测，对阿昔洛韦的降解率为97.1％。
实施例14
参考实施例13，其他参数不变，所述磁性氧化石墨烯催化粒子电极经分离、干燥后重复使用，经十次循环使用后，对阿昔洛韦的去除率仍有92％。
从实施例1-14中可以看出，所述基于磁性氧化石墨烯催化粒子电极三维电芬顿降解水中抗病毒药物残留的方法在不同初始pH，含有天然有机物的水质条件下，对不同种抗病毒药物都有较高的降解率。该方法适用范围广，处理时间短，催化剂可重复利用，具有较高的工程应用价值。

Claims (6)

  1. 一种基于磁性氧化石墨烯催化粒子电极三维电芬顿降解水中抗病毒药物残留的方法，其特征在于，该方法包括以下步骤：在三维电芬顿反应容器中，加入0.005～0.08mol/LNa 2SO 4电解质溶液、磁性氧化石墨烯催化粒子电极和含抗病毒药物残留的水，三维电芬顿反应器中催化粒子电极的投加量为5～45g/L，含抗病毒药物残留的水中抗病毒药物的浓度为15～25mg/L，调节电极板间距为2-6cm，施加电压为5～30V，控制三维电芬顿电解池的初始pH值为3～11，开启曝气，曝气强度为0.4～12L/min，对水中抗病毒药物残留降解；
    所述磁性氧化石墨烯催化粒子电极的制备方法包括以下步骤：
    步骤S1:称取蒙脱土和单层氧化石墨烯粉末于烧杯中，蒙脱土和单层氧化石墨烯粉末的质量比为3：(1～1.5)，加入乙二醇，经过超声后形成棕黄色的均匀悬浊液；
    步骤S2:称取FeCl 3·6H 2O、无水乙酸钠、聚乙二醇于烧杯中，FeCl 3·6H 2O、无水乙酸钠和聚乙二醇的质量比为1：(3.5～3.8)：(1.8～2.2)，加入乙二醇进行简单混合，然后加入步骤S1得到的悬浊液中，搅拌，将搅拌均匀的溶液放入聚四氟乙烯高压反应釜中加热，加热温度为150～250℃，加热时间为7～9h，得到黑色固体先用乙醇洗涤多次，在真空干燥箱中45～55℃干燥7.5～8.5h后使用研钵研磨，过80～120目筛后得到黑色粉末；
    步骤S3:将黑色粉末与4wt％聚乙烯醇水溶液混合，黑色粉末与4wt％聚乙烯醇水溶液的质量比为(2～2.5)：1，使用出条器挤出直径为5～7mm长条，放置于搓丸板上进行造粒，得到直径为5～7mm圆形颗粒；将圆形颗粒冷冻干燥，并在N 2保护气氛下550～650℃煅烧100～150min，最终得到直径为4.8～5.5mm的磁性氧化石墨烯催化粒子电极。
  2. 根据权利要求1所述基于磁性氧化石墨烯催化粒子电极三维电芬顿降解水中抗病毒药 物残留的方法，其特征在于，步骤S1，加入乙二醇的体积为45～55ml，超声时间为55～65min。
  3. 根据权利要求1所述基于磁性氧化石墨烯催化粒子电极三维电芬顿降解水中抗病毒药物残留的方法，其特征在于，步骤S2，加入乙二醇的体积为20～30ml，搅拌的时间为55～65min。
  4. 根据权利要求1所述基于磁性氧化石墨烯催化粒子电极三维电芬顿降解水中抗病毒药物残留的方法，其特征在于，所述抗病毒药物包括阿昔洛韦、阿比朵尔。
  5. 根据权利要求4所述基于磁性氧化石墨烯催化粒子电极三维电芬顿降解水中抗病毒药物残留的方法，其特征在于，当抗病毒药物为阿昔洛韦，体系中还加入20mg/L的腐殖酸。
  6. 一种磁性氧化石墨烯催化粒子电极的制备方法，其特征在于包括以下步骤：
    步骤S1:称取蒙脱土和单层氧化石墨烯粉末于烧杯中，蒙脱土和单层氧化石墨烯粉末的质量比为3：(1～1.5)，加入乙二醇，经过超声后形成棕黄色的均匀悬浊液；
    步骤S2:称取FeCl 3·6H 2O、无水乙酸钠、聚乙二醇于烧杯中，FeCl 3·6H 2O、无水乙酸钠和聚乙二醇的质量比为1：(3.5～3.8)：(1.8～2.2)，加入乙二醇进行简单混合，然后加入步骤S1得到的悬浊液中，搅拌，将搅拌均匀的溶液放入聚四氟乙烯高压反应釜中加热，加热温度为150～250℃，加热时间为7～9h，得到黑色固体先用乙醇洗涤多次，在真空干燥箱中45～55℃干燥7.5～8.5h后使用研钵研磨，过80～120目筛后得到黑色粉末；
    步骤S3:将黑色粉末与4wt％聚乙烯醇水溶液混合，黑色粉末与4wt％聚乙烯醇水溶液的质量比为(2～2.5)：1，使用出条器挤出直径为5～7mm长条，放置于搓丸板上进行造 粒，得到直径为5～7mm圆形颗粒；将圆形颗粒冷冻干燥，并在N 2保护气氛下550～650℃煅烧100～150min，最终得到直径为4.8～5.5mm的磁性氧化石墨烯催化粒子电极。
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Publication number Priority date Publication date Assignee Title
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Citations (7)

* Cited by examiner, † Cited by third party
Publication number Priority date Publication date Assignee Title
CN108160076A (zh) * 2017-12-07 2018-06-15 广东省工程技术研究所 一种磁性石墨烯基Fen+非均相催化剂制备方法及其应用
CN108816185A (zh) * 2018-07-27 2018-11-16 烟台大学 一种用于去除水中污染物的易分离型粘土吸附剂及其制备方法
CN109107531A (zh) * 2018-09-05 2019-01-01 宁夏大学 去除水溶液中盐酸四环素的磁性氧化石墨烯复合材料及其制备方法
CN109626518A (zh) * 2018-12-28 2019-04-16 广东省工程技术研究所 磁性石墨烯基Fen+三维电极非均相电Fenton处理印染废水的方法
US20200024162A1 (en) * 2019-03-28 2020-01-23 Central South University Method and device for sewage treatment
CN110841642A (zh) * 2019-12-03 2020-02-28 哈尔滨工业大学 一种超小四氧化三铁致密包覆三维还原氧化石墨烯类芬顿催化剂的制备方法
CN111003757A (zh) * 2019-11-14 2020-04-14 中海油天津化工研究设计院有限公司 一种磁性石墨烯气凝胶粒子电极及其制备方法

Family Cites Families (7)

* Cited by examiner, † Cited by third party
Publication number Priority date Publication date Assignee Title
US10396365B2 (en) * 2012-07-18 2019-08-27 Printed Energy Pty Ltd Diatomaceous energy storage devices
CN102775140B (zh) * 2012-08-11 2013-09-25 深圳市华水环保科技有限公司 一种离子筛型导电陶瓷母粒制备方法
CN106809921B (zh) * 2017-01-17 2020-04-17 广西大学 一种高岭土基三维粒子电极的制备方法
CN109755570A (zh) * 2017-11-06 2019-05-14 北京碳阳科技有限公司 三维复合电极材料及其制备方法、电极和储能器件
CN110639240A (zh) * 2019-09-24 2020-01-03 中国科学院兰州化学物理研究所 一种磁性无机黏土-石墨烯复合破乳材料的制备及其应用
CN111320240A (zh) * 2020-02-27 2020-06-23 石河子大学 一种用于处理染料废水的Fe-Mt三维粒子电极的制备方法及应用
CN111704262A (zh) * 2020-05-18 2020-09-25 华东理工大学 一种抗生素废水的磁分离处理净化方法

Patent Citations (7)

* Cited by examiner, † Cited by third party
Publication number Priority date Publication date Assignee Title
CN108160076A (zh) * 2017-12-07 2018-06-15 广东省工程技术研究所 一种磁性石墨烯基Fen+非均相催化剂制备方法及其应用
CN108816185A (zh) * 2018-07-27 2018-11-16 烟台大学 一种用于去除水中污染物的易分离型粘土吸附剂及其制备方法
CN109107531A (zh) * 2018-09-05 2019-01-01 宁夏大学 去除水溶液中盐酸四环素的磁性氧化石墨烯复合材料及其制备方法
CN109626518A (zh) * 2018-12-28 2019-04-16 广东省工程技术研究所 磁性石墨烯基Fen+三维电极非均相电Fenton处理印染废水的方法
US20200024162A1 (en) * 2019-03-28 2020-01-23 Central South University Method and device for sewage treatment
CN111003757A (zh) * 2019-11-14 2020-04-14 中海油天津化工研究设计院有限公司 一种磁性石墨烯气凝胶粒子电极及其制备方法
CN110841642A (zh) * 2019-12-03 2020-02-28 哈尔滨工业大学 一种超小四氧化三铁致密包覆三维还原氧化石墨烯类芬顿催化剂的制备方法

Non-Patent Citations (1)

* Cited by examiner, † Cited by third party
Title
ZHANG, BO ET AL.: "Hydrothermal synthesis of a graphene/magnetite/montmorillonite nanocomposite and its ultrasonically assisted methylene blue adsorption", JOURNAL OF MATERIALS SCIENCE, vol. 54, 10 May 2019 (2019-05-10), pages 11037 - 11055, XP036794102, ISSN: 1573-4803, DOI: 10.1007/s10853-019-03659-6 *

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