CN111547819B - Method for electrochemically recycling hexavalent chromium by using CuS modified carbon cloth electrode - Google Patents
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Abstract
A method for electrochemically recycling hexavalent chromium by using a CuS modified carbon cloth electrode relates to a method for electrochemically recycling hexavalent chromium. The invention aims to solve the technical problems of low removal rate and low removal rate of hexavalent chromium by the existing electrochemical method. The CuS modified carbon cloth electrode prepared by the invention has a high electrochemical active area, is beneficial to electron transmission, can quickly reduce hexavalent chromium into nontoxic trivalent chromium, can adsorb the trivalent chromium with positive electricity, and can adsorb 90% of the trivalent chromium when being degraded for 2 hours. According to the invention, the CuS modified carbon cloth electrode presenting negative charges efficiently adsorbs positively charged trivalent chromium through the electrostatic adsorption effect, so that the chromium resource is recovered. The electrochemical technology used by the invention is simple, rapid and green, and has no secondary pollution. The method is applied to removing hexavalent chromium in the sewage and recovering trivalent chromium.
Description
Technical Field
The invention relates to a method for electrochemically recovering hexavalent chromium.
Background
The pollutants are various in the world, but heavy metal pollutants are always of great importance, and the heavy metal pollutants seriously harm the health of human beings and other animals and plants. Heavy metal contaminants pose a serious threat to the environment if left untreated in rivers. Chromium is a serious harmful one of heavy metal pollutants, is just a key treatment object in various countries, and has strict regulations on chromium-related waste water discharge and chromium content in drinking water. Wherein, the total amount of chromium discharged by wastewater is not more than 1.5mg/L and hexavalent chromium is less than 0.5mg/L as specified in Integrated wastewater discharge Standard (GB8978-1996) in China, and the maximum content of hexavalent chromium in drinking water is 0.05mg/L as specified in sanitary Standard for Drinking Water (GB 5749-2006). Chromium is not only prevalent and highly toxic, but is also most commonly found in hazardous waste locationsOne of 10 groundwater contaminants was detected, which is also one of the 14 most toxic heavy metals. The world cancer society has long classified hexavalent chromium compounds as a very carcinogenic substance. Hexavalent chromium, if exposed directly to the air, can cause a variety of diseases and can increase the incidence of both lung and gastric cancer in animals and humans. Humans and animals also suffer from serious illness due to absorption by the digestive tract or exposure of the skin to water contaminated with hexavalent chromium. For Cr at present6+The removal method comprises physical adsorption, chemical chromium repair, sulfide reduction, ferric salt, electrocoagulation, biological chromium repair and other methods, but all have the following defects: for example, the chemical repair process is influenced by pH in a large range, and has an effect under an acidic condition, but the removal rate cannot reach the completeness; similarly, the removal rate of chromium by the ferric salt method and the electrocoagulation method cannot achieve the purpose of complete removal, and the bioremediation method cannot be widely used due to the limitation of conditions. On the basis, the defects of various fields are combined, the cheap material with the conductive performance and the combined material for electrochemical repair compensate the defects, the electrocatalysis is considered as the best reduction method, and the combination of the modification and the electrochemistry of the cheap carbon cloth material shows that the Cr removal is good6+Performance, for increasing Cr6+The removal rate and the wide application lay a foundation.
Due to the existence of a plurality of forms, the valence state of chromium is widely distributed, generally ranging from-2 to +6, but the main form is Cr3+And Cr6+. The toxicity of chromium varies with its valence and varies widely. Cr (chromium) component3+Mainly made of Cr (OH)3The colloid is precipitated in neutral or alkaline environment and stably exists in the sludge, so the fluidity is poor, and the colloid is also an essential micronutrient element in human bodies and plays an important role in the growth and development, metabolic process and the like of human beings. Trivalent chromium is one of the main components of glucose tolerance factor in human body, and can increase the metabolism speed of sugar and fat in human body, soften blood vessel, reduce blood fat, reduce serum total cholesterol, increase high density lipoprotein beneficial to human body, and reduce low density lipoprotein and triglyceride not beneficial to human bodyThe acid ester also helps to ensure that the amount of trivalent chromium which needs to be taken in a day by an adult is 50-200 mug. Hexavalent chromium is readily soluble in water and is usually present in the oxyanion state (e.g., Cr)2O7 2-、CrO4 2-、HCrO4 -) Therefore, the mobility in water and soil is large. The toxicity of hexavalent chromium can be up to 100 times that of trivalent chromium based on the difference in properties between hexavalent chromium and trivalent chromium, and thus, the conversion of cr (vi) to cr (iii) under controlled conditions is an effective method for remediating cr (vi) contamination.
Reduction methods suitable for hexavalent chromium-containing wastewater include photocatalytic reduction, photoelectrocatalytic reduction, electrochemical reduction, and chemical reduction, in which either high energy or a chemical reducing agent is required, which complicates the process of reducing hexavalent chromium and may cause secondary pollution to the environment by the chemical agent added thereto. Electrochemical removal of heavy metals from wastewater is a clean process that does not produce secondary pollutants. Therefore, it is highly desirable to reduce hexavalent chromium to trivalent chromium using an electrochemical process and recover the trivalent chromium.
Reducing sulphides is a common reducing agent and semiconducting chalcogenides nanostructures have great potential for use in different fields, especially copper chalcogenides, due to their special optical and electronic properties. Copper sulfide (CuS) has found applications in many areas due to its low toxicity, low cost, broad composition and crystal structure.
Disclosure of Invention
The invention provides a method for electrochemically recycling hexavalent chromium by using a CuS modified carbon cloth electrode, aiming at solving the technical problems of low removal rate and low removal rate of hexavalent chromium removed by the existing electrochemical method.
The method for electrochemically recycling hexavalent chromium by using the CuS modified carbon cloth electrode is carried out according to the following steps:
firstly, soaking carbon cloth in concentrated nitric acid water solution for 24-25 h, then washing the carbon cloth to be neutral by deionized water, and drying the carbon cloth for 2-2.5 h at the temperature of 80-85 ℃ to obtain acidic carbon cloth;
dissolving copper sulfate pentahydrate and thioacetamide into deionized water, stirring for 30-40 min to obtain a mixed solution, then putting the mixed solution into a polytetrafluoroethylene high-pressure kettle, completely immersing the acidic carbon cloth prepared in the step one into the mixed solution, reacting for 12-13 h at 180-190 ℃, taking out the carbon cloth, washing with the deionized water, and drying for 3-4 h at 80-90 ℃ to obtain a CuS modified carbon cloth electrode;
the mass ratio of the copper sulfate pentahydrate to the thioacetamide is 1 (1-1.2);
the volume ratio of the weight of the copper sulfate pentahydrate to the deionized water is 1g (150 mL-170 mL);
and thirdly, taking the CuS modified carbon cloth electrode prepared in the second step as a working electrode, a platinum electrode as a counter electrode, an Ag/AgCl electrode as a reference electrode, and taking the hexavalent chromium-containing metal wastewater to be degraded as electrolyte to form a three-electrode system, wherein the hexavalent chromium-containing metal wastewater is degraded under the voltage of-1V to-1.3V, and the degradation time is 2h to 3 h.
The CuS modified carbon cloth electrode prepared by the invention has a high electrochemical active area, is beneficial to electron transmission, can quickly reduce hexavalent chromium into nontoxic trivalent chromium, can adsorb the trivalent chromium with positive electricity, and can adsorb 90% of the trivalent chromium when being degraded for 2 hours.
The invention has the following advantages:
1. the electrochemical technology used by the invention is simple, rapid and green, and has no secondary pollution;
2. according to the invention, the semiconductor nano CuS with reducibility is loaded on the carbon cloth electrode, so that the electrochemical active area of the carbon cloth electrode is increased, the electron transmission efficiency is accelerated, hexavalent chromium in wastewater is efficiently removed, and the highly toxic hexavalent chromium is converted into non-toxic trivalent chromium; the removing efficiency of the CuS modified carbon cloth electrode on hexavalent chromium is 29.9 times that of a bare carbon cloth electrode; the adsorption efficiency of the CuS modified carbon cloth electrode on trivalent chromium is 4.8 times that of a bare carbon cloth electrode;
3. according to the invention, the CuS modified carbon cloth electrode which presents negative charges can efficiently adsorb trivalent chromium with positive charges through the electrostatic adsorption effect, so that the recovery of chromium resources is realized;
4. the invention provides a new idea for the design and manufacture of the carbon cloth electrode and provides a new idea for the application of the carbon cloth electrode in an electrochemical system.
Drawings
FIG. 1 is an SEM image of a carbon cloth without any treatment at step one of experiment one, at a magnification of 10000 times;
fig. 2 is an SEM image of the CuS modified carbon cloth electrode prepared in step two of experiment one, magnified 10000 times;
FIG. 3 is a comparison graph of the removal rate of hexavalent chromium by the bare carbon cloth electrode in test two and the CuS modified carbon cloth electrode in test one;
FIG. 4 is a graph comparing the removal rates of the bare carbon cloth electrode in test two and the CuS modified carbon cloth electrode in test one for chromium;
FIG. 5 is a cyclic voltammogram;
FIG. 6 is a graph of removal rate versus time;
fig. 7 is an XPS plot of the S element in the CuS modified carbon cloth electrode before and after 2h of degradation in step three of experiment one.
Detailed Description
The first embodiment is as follows: the embodiment is a method for electrochemically recycling hexavalent chromium by using a CuS modified carbon cloth electrode, which is specifically carried out according to the following steps:
firstly, soaking carbon cloth in concentrated nitric acid water solution for 24-25 h, then washing the carbon cloth to be neutral by deionized water, and drying the carbon cloth for 2-2.5 h at the temperature of 80-85 ℃ to obtain acidic carbon cloth;
dissolving copper sulfate pentahydrate and thioacetamide into deionized water, stirring for 30-40 min to obtain a mixed solution, then putting the mixed solution into a polytetrafluoroethylene high-pressure kettle, completely immersing the acidic carbon cloth prepared in the step one into the mixed solution, reacting for 12-13 h at 180-190 ℃, taking out the carbon cloth, washing with the deionized water, and drying for 3-4 h at 80-90 ℃ to obtain a CuS modified carbon cloth electrode;
the mass ratio of the copper sulfate pentahydrate to the thioacetamide is 1 (1-1.2);
the volume ratio of the weight of the copper sulfate pentahydrate to the deionized water is 1g (150 mL-170 mL);
and thirdly, taking the CuS modified carbon cloth electrode prepared in the second step as a working electrode, a platinum electrode as a counter electrode, an Ag/AgCl electrode as a reference electrode, and taking the hexavalent chromium-containing metal wastewater to be degraded as electrolyte to form a three-electrode system, wherein the hexavalent chromium-containing metal wastewater is degraded under the voltage of-1V to-1.3V, and the degradation time is 2h to 3 h.
The second embodiment is as follows: the first difference between the present embodiment and the specific embodiment is: the carbon cloth model described in the first step was HCP 331N. The rest is the same as the first embodiment.
The third concrete implementation mode: the present embodiment differs from the first or second embodiment in that: the mass fraction of the concentrated nitric acid aqueous solution in the first step is 69%. The others are the same as in the first or second embodiment.
The fourth concrete implementation mode: the difference between this embodiment mode and one of the first to third embodiment modes is: and in the second step, reacting at 180 ℃ for 12h, taking out the carbon cloth, washing with deionized water, and drying at 80 ℃ for 3h to obtain the CuS modified carbon cloth electrode. The rest is the same as one of the first to third embodiments.
The fifth concrete implementation mode: the fourth difference between this embodiment and the specific embodiment is that: the mass ratio of the copper sulfate pentahydrate to the thioacetamide in the step two is 1: 1. The rest is the same as the fourth embodiment.
The sixth specific implementation mode: the fifth embodiment is different from the fifth embodiment in that: the volume ratio of the mass of the copper sulfate pentahydrate to the deionized water in the step two is 1g:150 mL. The rest is the same as the fifth embodiment.
The seventh embodiment: the sixth embodiment is different from the sixth embodiment in that: degrading under the voltage of-1.2V in the third step, wherein the degradation time is 2 h. The rest is the same as the sixth embodiment.
The invention was verified with the following tests:
test one: the test is a method for electrochemically recovering hexavalent chromium by using a CuS modified carbon cloth electrode, and is specifically carried out according to the following steps:
firstly, cutting carbon cloth into 3cm multiplied by 4cm, wherein each carbon cloth is about 0.2g, and putting two carbon cloths in total into 20mL concentrated nitric acid water solution for soaking for 24h, then washing the carbon cloths to be neutral by deionized water, and drying the carbon cloths for 2h at 80 ℃ to obtain acidic carbon cloth; the carbon cloth model is HCP 331N; the mass fraction of the concentrated nitric acid aqueous solution is 69%;
secondly, dissolving 0.2g of blue vitriol and 0.2g of thioacetamide together in 30mL of deionized water, stirring for 30min to obtain a mixed solution, then putting the mixed solution into a 100mL polytetrafluoroethylene autoclave, completely immersing the two acidic carbon cloths prepared in the first step into the mixed solution, reacting for 12h at 180 ℃, taking out the carbon cloths, washing with deionized water, and drying for 3h at 80 ℃ to obtain a CuS modified carbon cloth electrode;
pouring 10mL of potassium dichromate aqueous solution into a 100mL electrolytic cell, pouring 20mL of 0.5mol/L sodium sulfate aqueous solution into the electrolytic cell, and pouring 70mL of deionized water into the electrolytic cell to obtain a hexavalent chromium solution with the chromium concentration of 10 mg/L; the concentration of chromium element in the potassium dichromate water solution is 100 mg/L;
and (3) taking the CuS modified carbon cloth electrode prepared in the step two as a working electrode, a platinum electrode as a counter electrode, an Ag/AgCl electrode as a reference electrode, and taking the prepared hexavalent chromium solution with the chromium element concentration of 10mg/L as electrolyte to form a three-electrode system, and degrading under the voltage of-1.2V for 2h to finish the degradation of hexavalent chromium.
Fig. 1 is an SEM image of the carbon cloth without any treatment in the first step of the first test at 10000 times magnification, and it is apparent that the fiber surface of the bare carbon cloth is very smooth.
Fig. 2 is an SEM image of the CuS-modified carbon cloth electrode prepared in the second step of the first test, which is magnified 10000 times, compared to the bare carbon cloth with a dense and smooth surface (fig. 1), the surface of the CuS-modified carbon cloth becomes rougher due to the loading of the nano CuS.
And (2) test II: this test is a comparative test: the method specifically comprises the following steps:
firstly, cutting a carbon cloth into 3cm multiplied by 4cm, wherein each piece of carbon cloth is about 0.2 g; the carbon cloth model is HCP 331N;
pouring 10mL of potassium dichromate aqueous solution into a 100mL electrolytic cell, pouring 20mL of 0.5mol/L sodium sulfate aqueous solution into the electrolytic cell, and pouring 70mL of deionized water into the electrolytic cell to obtain a hexavalent chromium solution with the chromium concentration of 10 mg/L; the concentration of chromium element in the potassium dichromate water solution is 100 mg/L;
and (2) taking the two pieces of carbon cloth cut in the step one as a working electrode, a platinum electrode as a counter electrode, an Ag/AgCl electrode as a reference electrode, and taking the prepared hexavalent chromium solution with the chromium element concentration of 10mg/L as electrolyte to form a three-electrode system, and degrading under the voltage of-1.2V for 2 hours to finish the degradation of hexavalent chromium.
And measuring the concentration of hexavalent chromium in the electrolytic cell after degradation in the first test and the second test by using an ultraviolet spectrophotometer.
FIG. 3 is a comparison graph of the removal rates of hexavalent chromium from the bare carbon cloth electrode in test two and the CuS modified carbon cloth electrode in test one, where Ct is the concentration of hexavalent chromium in the electrolytic cell after t-time degradation, and C is the concentration of hexavalent chromium in the electrolytic cell0The concentration of hexavalent chromium in the electrolytic cell when the hexavalent chromium is not degraded; the curve 1 is a bare carbon cloth electrode, the curve 2 is a CuS modified carbon cloth electrode, and it can be seen from the figure that the bare carbon cloth only reduces less than 15% of hexavalent chromium after reacting for 20min, and the reduction rate of hexavalent chromium after degrading for 2h only reaches less than 55%; the CuS modified carbon cloth electrode can reduce about 92% of hexavalent chromium after reacting for 10min, can reduce 99.4% of hexavalent chromium after reacting for 20min, and can reach 100% in the follow-up process, and the reduction rate and the reduction degree of the CuS modified carbon cloth electrode far exceed the effect of bare carbon cloth on hexavalent chromium reduction.
And measuring the total concentration of the chromium element in the electrolytic cell after degradation in the first test and the second test by using an atomic absorption spectrophotometer.
FIG. 4 is a comparison graph of the removal rates of the chromium element in the bare carbon cloth electrode in the second test and the CuS modified carbon cloth electrode in the first test, where Ct is the total concentration of the chromium element in the electrolytic cell after t time of degradation, and C is0The total concentration of chromium element in the electrolytic cell when the electrolytic cell is not degraded; curve 1 is a bare carbon cloth electrode, and curve 2 is a CuS modified carbon cloth electrode; during the degradation process, hexavalent chromium is reduced to trivalent chromium, and because the position of the working electrode is the cathode, the working electrode does not adsorb hexavalent chromium (Cr) with negative charge2O7 2-) Thus, the reduction of the concentration of chromium in the cell is in fact a reduction of the concentration of trivalent chromium in the cell, i.e. the amount of trivalent chromium adsorbed on the surface of the working electrode; it can be seen from the figure that, in terms of efficiency of adsorbing and recovering trivalent chromium, the trivalent chromium adsorbed by the CuS modified carbon cloth electrode when degraded for 20min is equivalent to the trivalent chromium adsorbed by the bare carbon cloth electrode for 2h, and to the extent of adsorption and recovery, the CuS modified carbon cloth electrode can adsorb 90% of the trivalent chromium when degraded for 2h, which has reached a very high recovery rate.
And (3) test III: this test differs from the test one in that: in the third step, the cyclic voltammetry test is carried out at the scanning rate of-1.2V-0V and 100 mV/s. The rest is the same as test one.
And (4) testing: the difference between this test and the second test is that: in the third step, the cyclic voltammetry test is carried out at the scanning rate of-1.2V-0V and 100 mV/s. The rest was the same as in test two.
FIG. 5 is a cyclic voltammogram, with curve 1 being run four and curve 2 being run three. It can be seen from the figure that the scanning area of the CuS modified carbon cloth electrode is far larger than that of the bare carbon cloth electrode, that is, the electrochemical active area of the CuS modified carbon cloth electrode is far larger than that of the bare carbon cloth electrode, which is more beneficial to the transmission of electrons, so that the CuS modified carbon cloth electrode can rapidly and efficiently reduce hexavalent chromium.
The reaction rate k is calculated by the following formula 1, the reaction rate k can represent the removal rate of the object to be removed, the reaction rates k of the respective time points are calculated by taking a plurality of time points, the reaction rates k of the whole reaction are obtained by linear fitting, the removal rates k of hexavalent chromium in the first test and the second test and the removal rates k of chromium element in the first test and the second test are calculated respectively.
Equation 1: ln (C)0K is reaction rate, t is reaction time, Ct is concentration of the substance to be measured at the time of reaction t, C0Is the initial concentration of the analyte.
FIG. 6 is a graph comparing removal rates, wherein the left graph is the removal efficiency of hexavalent chromium, the right graph is the removal efficiency of chromium, group 1 is test two, and group 2 is test one. It can be seen from the figure that the removal efficiency of the CuS modified carbon cloth electrode on hexavalent chromium is 29.9 times that of the bare carbon cloth electrode (left figure), and the improvement is possessed because of the huge improvement of the electrochemical active area of the CuS modified carbon cloth electrode (figure 5); the cathode where the working electrode is located can produce nonspecific adsorption on the trivalent chromium with positive charge, the specific adsorption brought by the CuS modification expands the adsorption efficiency, and the adsorption efficiency of the CuS modified carbon cloth electrode on the trivalent chromium is 4.8 times that of a bare carbon cloth electrode (right picture).
FIG. 7 is an XPS diagram of the S element in the CuS modified carbon cloth electrode before and after 2h degradation in the third step of the first test, wherein after 2h degradation in the curve 1 and before 2h degradation, it can be seen from the XPS diagram that some oxygen-containing functional groups exist in the bare carbon cloth after being activated by concentrated nitric acid and in the hydrothermal reaction at a high temperature of 180 ℃, CuS is uniformly connected to the surface of the carbon cloth through the oxygen-containing functional groups, and-O-Cu-S is used as-O-Cu-S-Is a fixed site with Cr, and the obvious shift of the position of S before and after degradation can be seen from XPS, which proves that the electronic environment of S is changed due to the combination of Cr and S.
Claims (7)
1. A method for electrochemically recycling hexavalent chromium by using a CuS modified carbon cloth electrode is characterized by comprising the following steps:
firstly, soaking carbon cloth in concentrated nitric acid water solution for 24-25 h, then washing the carbon cloth to be neutral by deionized water, and drying the carbon cloth for 2-2.5 h at the temperature of 80-85 ℃ to obtain acidic carbon cloth;
dissolving copper sulfate pentahydrate and thioacetamide into deionized water, stirring for 30-40 min to obtain a mixed solution, then putting the mixed solution into a polytetrafluoroethylene high-pressure kettle, completely immersing the acidic carbon cloth prepared in the step one into the mixed solution, reacting for 12-13 h at 180-190 ℃, taking out the carbon cloth, washing with the deionized water, and drying for 3-4 h at 80-90 ℃ to obtain a CuS modified carbon cloth electrode;
the mass ratio of the copper sulfate pentahydrate to the thioacetamide is 1 (1-1.2);
the volume ratio of the weight of the copper sulfate pentahydrate to the deionized water is 1g (150 mL-170 mL);
and thirdly, taking the CuS modified carbon cloth electrode prepared in the second step as a working electrode, a platinum electrode as a counter electrode, an Ag/AgCl electrode as a reference electrode, and taking the hexavalent chromium-containing metal wastewater to be degraded as electrolyte to form a three-electrode system, wherein the hexavalent chromium-containing metal wastewater is degraded under the voltage of-1V to-1.3V, and the degradation time is 2h to 3 h.
2. The process of claim 1 wherein said carbon cloth of step one is HCP 331N.
3. The method of claim 1 wherein said concentrated aqueous nitric acid solution of step one is 69% by weight.
4. The method of claim 1 wherein in step two, the reaction is carried out at 180 ℃ for 12 hours, then the carbon cloth is taken out and washed with deionized water, and then dried at 80 ℃ for 3 hours to obtain the CuS modified carbon cloth electrode.
5. The method for electrochemically recovering hexavalent chromium using a CuS-modified carbon cloth electrode according to claim 1, wherein the mass ratio of copper sulfate pentahydrate to thioacetamide in the second step is 1: 1.
6. The method of claim 1 wherein the mass to volume ratio of copper sulfate pentahydrate to deionized water in step two is 1g:150 mL.
7. The method for electrochemical recovery of hexavalent chromium using a CuS-modified carbon cloth electrode according to claim 1, wherein the degradation is performed at a voltage of-1.2V for a degradation time of 2 hours in step three.
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Citations (7)
| Publication number | Priority date | Publication date | Assignee | Title |
|---|---|---|---|---|
| US3892833A (en) * | 1972-11-10 | 1975-07-01 | Matsushita Electric Ind Co Ltd | Method of making an ion-selective electrode |
| CN101634039A (en) * | 2009-09-01 | 2010-01-27 | 南京大学 | Glassy carbon electrode (GCE) modified by conductive copolymer, preparation method thereof and method for removing dichromate from water |
| CN103623845A (en) * | 2013-12-17 | 2014-03-12 | 扬州大学 | Preparation method of nanocomposite photocatalyst for processing wastewater containing hexavalent chromium |
| CN108039281A (en) * | 2017-11-15 | 2018-05-15 | 哈尔滨理工大学 | Preparation method of the multi-walled carbon nanotube base CuS quantum dots to electrode |
| CN110078280A (en) * | 2019-05-24 | 2019-08-02 | 安徽工程大学 | A kind of synchronous method and its application for removing low concentration citric acid complex copper and Cr VI in waste water |
| CN110563094A (en) * | 2019-09-17 | 2019-12-13 | 南昌航空大学 | application of sulfonated carbon cloth electrode |
| CN110697706A (en) * | 2019-10-08 | 2020-01-17 | 北京化工大学 | Preparation method of three-dimensional biomass carbon/copper sulfide used as electrode material |
Family Cites Families (1)
| Publication number | Priority date | Publication date | Assignee | Title |
|---|---|---|---|---|
| US20200070094A1 (en) * | 2016-12-21 | 2020-03-05 | University Of Iowa Research Foundation | Apparatus and method for three-dimensional photo-electrodialysis |
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Patent Citations (7)
| Publication number | Priority date | Publication date | Assignee | Title |
|---|---|---|---|---|
| US3892833A (en) * | 1972-11-10 | 1975-07-01 | Matsushita Electric Ind Co Ltd | Method of making an ion-selective electrode |
| CN101634039A (en) * | 2009-09-01 | 2010-01-27 | 南京大学 | Glassy carbon electrode (GCE) modified by conductive copolymer, preparation method thereof and method for removing dichromate from water |
| CN103623845A (en) * | 2013-12-17 | 2014-03-12 | 扬州大学 | Preparation method of nanocomposite photocatalyst for processing wastewater containing hexavalent chromium |
| CN108039281A (en) * | 2017-11-15 | 2018-05-15 | 哈尔滨理工大学 | Preparation method of the multi-walled carbon nanotube base CuS quantum dots to electrode |
| CN110078280A (en) * | 2019-05-24 | 2019-08-02 | 安徽工程大学 | A kind of synchronous method and its application for removing low concentration citric acid complex copper and Cr VI in waste water |
| CN110563094A (en) * | 2019-09-17 | 2019-12-13 | 南昌航空大学 | application of sulfonated carbon cloth electrode |
| CN110697706A (en) * | 2019-10-08 | 2020-01-17 | 北京化工大学 | Preparation method of three-dimensional biomass carbon/copper sulfide used as electrode material |
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