Method for electrochemically treating biogas slurry after anaerobic fermentation of kitchen waste

Abstract

The application discloses a method for electrochemically treating anaerobic fermentation biogas slurry of kitchen waste, mainly comprising the following steps: 1. removing organic matters in the anaerobic fermentation biogas slurry of kitchen waste by electrochemical oxidation, thereby reducing the ammonia nitrogen content and COD value of the biogas slurry; 2. reducing residual hypochlorite in the biogas slurry after electrochemical oxidation in step 1 into chloride ions by a thermal decomposition method, a photo decomposition method or a catalytic decomposition method; 3. constructing a capacitor by using a chloride ion adsorption material and a sodium ion embedded electrode material, and adsorbing sodium chloride in the biogas slurry in step 2 by the capacitor capacitive deionization method; 4. discharging the capacitor adsorbing sodium chloride in a sodium chloride storage tank to resolve the sodium chloride, and returning the capacitor to step 3 to adsorb sodium chloride again after discharging, and repeating the cycle for multiple times until the sodium chloride content in the biogas slurry reaches the discharge standard; compared with the mainstream treatment process of the current anaerobic fermentation biogas slurry of kitchen waste, the method can greatly reduce energy consumption.

Description

Technical Field

[0001] This invention relates to the field of electrochemical water treatment technology, specifically a method for electrochemically treating biogas slurry after anaerobic fermentation of kitchen waste. Background Technology

[0002] With the introduction of a series of environmental protection issues such as "carbon neutrality and carbon peaking", garbage sorting has gradually come into people's view in recent years. Due to the gradual improvement of people's living conditions, the rapid growth of the service industry, especially the rapid rise of the food delivery industry, the amount of kitchen waste generated has been increasing year by year. As a pilot city for garbage sorting, Nanjing has taken the lead in vigorously developing scientific methods for the treatment of sorted garbage.

[0003] Food waste refers to leftover scraps from food processing in restaurants, hotels, and staff canteens, as well as leftover food from tables, processing waste from fast food products, and animal and vegetable oils that cannot be directly used. Food waste has a high water content and must be treated promptly; otherwise, it will decompose and cause pollution to the environment.

[0004] Currently, the mainstream food waste treatment process involves first using equipment to sort the food waste to remove non-biodegradable materials such as plastics. After the oil phase is separated by settling, the remaining waste is crushed and then treated through biochemical processes, ultrafiltration, nanofiltration, and reverse osmosis. The desalinated water is discharged directly, while the concentrated water is treated by MVR evaporation. MVR evaporation technology requires approximately 15 kW / h to 55 kW / h of electricity to evaporate one ton of water, a range that considers different operating conditions and material properties. Compared to traditional multi-effect evaporators, MVR evaporators do have a significant advantage in energy consumption. However, for the large and increasing volume of food waste wastewater, MVR evaporation remains the most energy-intensive method in food waste treatment. Furthermore, the solids remaining after MVR evaporation are a mixture of organic matter and salts, which is hazardous waste, adding to the treatment costs. Therefore, in order to save energy, there is an urgent need to propose an alternative method to MVR evaporation concentration. Summary of the Invention

[0005] The purpose of this invention is to provide a method for electrochemically treating biogas slurry after anaerobic fermentation of kitchen waste, so as to solve the problems mentioned in the background art.

[0006] To achieve the above objectives, the present invention provides the following technical solution:

[0007] This invention provides a method for electrochemically treating biogas slurry from anaerobic fermentation of kitchen waste, comprising the following steps:

[0008] Step 1: Remove organic matter from the anaerobic fermentation slurry of kitchen waste through electrochemical oxidation, reduce the ammonia nitrogen content and COD value of the slurry, and meet the wastewater discharge standards;

[0009] Step 2: The remaining hypochlorite ions in the biogas slurry after electro-oxidation in Step 1 are reduced to chloride ions by chlorate decomposition, which facilitates further desalination of the biogas slurry.

[0010] Step 3: Construct a capacitor using chloride ion adsorption material and sodium ion intercalation electrode material, and adsorb sodium chloride from the biogas slurry in Step 2 at a voltage of -0.6V to -0.6V using a capacitive deionization method;

[0011] Step 4: Discharge the capacitor that adsorbs sodium chloride in the sodium chloride storage tank to desorb the sodium chloride. After discharge, return the capacitor to Step 3 to adsorb sodium chloride again. Repeat this cycle multiple times until the sodium chloride content in the biogas slurry meets the discharge standard.

[0012] Furthermore, in step one, the electrode material for the electrochemical oxidation is ruthenium-iridium, and the temperature condition is selected as 30-60℃ water bath heating. The electrolysis potential is determined by testing the bubble production rate of concentrated water samples based on different water samples. Different voltages are applied to the water samples, and the bubble generation rate is observed to select the most suitable voltage value and electrolysis time. By selecting the most suitable electrolysis potential and adjusting the electrochemical oxidation time and the sodium hypochlorite oxidation time for COD and ammonia nitrogen, the reaction equilibrium is maintained while saving energy.

[0013] Furthermore, in step one, the electrochemical oxidation site is 1.05V-1.25V (VS. SCE), and the electrolysis time is 20h.

[0014] Furthermore, in step two, the chlorate decomposition method is one or a combination of thermal decomposition, photodecomposition, and catalytic decomposition.

[0015] Furthermore, the catalyst used in the catalytic decomposition method is one or more of nickel oxide, cobalt oxide, copper oxide, and iron oxide; the mass ratio of the catalyst to the biogas slurry after electro-oxidation is 1:25-40. Preferably, the catalyst used in the catalytic decomposition method is nickel oxide powder doped with iron oxide powder, and the mass ratio of nickel oxide to iron oxide is 1:10-1:25 (preferably 1:19).

[0016] Furthermore, the photolysis method is performed at 300-800 W / m 2 Decomposes under light conditions.

[0017] Furthermore, the thermal decomposition method involves raising the temperature of the biogas slurry after electro-oxidation to 40-60℃; by increasing the initial temperature of the biogas slurry from the fermentation of kitchen waste, the concentration of ClO₂ is accelerated. - break down.

[0018] Preferably, in step two, the chlorate decomposition method is a combination of photodecomposition and catalytic decomposition.

[0019] Further, in step three, the chloride ion adsorption material includes an electric double layer adsorption material and a chloride ion conversion material; the sodium ion intercalation electrode material includes an electric double layer electrode material and a pseudocapacitive electrode material; the electric double layer electrode material is one or more of activated carbon, carbon fiber, carbon gel, and carbon nanotubes; the pseudocapacitive electrode material is one or more of graphite, Prussian blue, Prussian white, and ferric ferricyanide; and the chloride ion adsorption material is one or more of Ag composite material, Bi composite material, and Fe composite material.

[0020] Furthermore, in step four, the sodium chloride solution in the sodium chloride storage tank is a near-saturated sodium chloride solution at room temperature. That is, the sodium chloride solution in the storage tank has a concentration of 4.6 mol / L at 15-25°C.

[0021] Compared with the prior art, the beneficial effects of the present invention are:

[0022] (1) After the present invention uses an electrochemical method to treat the anaerobic fermentation biogas slurry of kitchen waste, the concentration of sodium chloride in the sodium chloride storage tank that needs to be treated by MVR is only about 10% of the concentration of reverse osmosis concentrate in the mainstream treatment process of fermentation biogas slurry, which greatly reduces the energy consumption of the evaporation process.

[0023] (2) In the mainstream treatment process of fermentation biogas slurry, the reverse osmosis concentrate contains high concentrations of organic matter, and a certain amount of organic matter will volatilize in the MVR process; while the wastewater after electrochemical oxidation of the present invention contains almost no organic matter, thus avoiding the risk of organic matter volatilization.

[0024] (3) In this invention, the sodium chloride concentrate in the sodium chloride storage tank can be sold as industrial-grade sodium chloride after MVR evaporation. However, the mainstream sodium chloride treatment process, MVR evaporation product, is sodium chloride with high organic concentration, which is hazardous waste.

[0025] (4) In the electrochemical oxidation process of step one of the present invention, hydrogen gas, a byproduct, is generated at the cathode, which further improves the economic efficiency of the process.

[0026] (5) In the present invention, the process of deionizing sodium chloride and storing the mains electricity in the process of sodium chloride desorption and discharge can recover part of the electrical energy consumed by sodium chloride adsorption. Attached Figure Description

[0027] Figure 1 This is a schematic diagram of a method for electrochemically treating biogas slurry from anaerobic fermentation of kitchen waste. Detailed Implementation

[0028] The technical solutions of the embodiments of the present invention will be clearly and completely described below with reference to the accompanying drawings. Obviously, the described embodiments are only some embodiments of the present invention, and not all embodiments. Based on the embodiments of the present invention, all other embodiments obtained by those skilled in the art without creative effort are within the scope of protection of the present invention.

[0029] like Figure 1 As shown, the present invention provides a technical solution: a method for electrochemically treating biogas slurry after anaerobic fermentation of kitchen waste, comprising the following steps:

[0030] Step 1: Remove organic matter from the anaerobic fermentation slurry of kitchen waste through electrochemical oxidation, reduce the ammonia nitrogen content and COD value of the slurry, and meet the wastewater discharge standards;

[0031] Step 2: The remaining hypochlorite ions in the biogas slurry after electro-oxidation in Step 1 are reduced to chloride ions by thermal decomposition, photodecomposition or catalytic decomposition, so as to facilitate further desalination of the biogas slurry.

[0032] Step 3: Construct a capacitor using chloride ion adsorption material and sodium ion intercalation electrode material, and adsorb sodium chloride from the biogas slurry in Step 2 by capacitive deionization method;

[0033] Step 4: Discharge the capacitor that adsorbs sodium chloride in the sodium chloride storage tank to desorb the sodium chloride. After discharge, return the capacitor to Step 3 to adsorb sodium chloride again. Repeat this cycle multiple times until the sodium chloride content in the biogas slurry meets the discharge standard. Example 1

[0034] Step 1: Take 1L of reverse osmosis concentrate from the anaerobic fermentation slurry of kitchen waste (ammonia nitrogen content 1000mg / L, COD value 820mg / L, sodium chloride concentration 35.4g / L). The electrode material for electrochemical oxidation is ruthenium-iridium material, the temperature condition is 60℃ water bath heating, the electrochemical oxidation potential is 1.05V (VS. SCE), and the electrolysis time is 20h. The ammonia nitrogen content and COD value after electrochemical oxidation are both 0mg / L, as measured by the ammonia nitrogen sodium reagent method and COD digestion tester.

[0035] Step 2: Add a mixed catalyst of NiO and Fe2O3 to the liquid after electro-oxidation in Step 1 at a NiO:Fe2O3 mass ratio of 1:19 and a solid-liquid mass ratio of 1:25. The catalyst is then heated at 800 W / m³. 2 The conversion rate of sodium hypochlorite was 98.4% after decomposition under light for 10 hours.

[0036] Step 3: A capacitor was constructed using a double-layer adsorption-coated BiOCl@MC material with a mass ratio of 10:9 and sodium ion embedded electrode material of iron ferricyanide nanocubic blocks. After multiple adsorption / desorption (electrolysis) by capacitive deionization, the sodium chloride concentration in the biogas slurry was reduced to 0.03 g / L.

[0037] Step 4: The capacitor that adsorbed sodium chloride was discharged and desorbed into the sodium chloride storage tank. After the desorption was completed, the sodium chloride concentration of the capacitor was measured to be 0 mg / L. The desorbed capacitor was then returned to Step 3 for recycling until the sodium chloride content in the solution met the discharge standard. The sodium chloride storage tank contained a sodium chloride solution with a concentration of 4.6 mol / L at 15-25℃. The sodium chloride storage tank was then subjected to MVR evaporation and concentration, requiring only 100 mL of water to be evaporated, which is 10% of the original water sample volume.

[0038] In step three, the double-layer adsorption coated BiOCl material is prepared by template method using agar as carbon source, bismuth nitrate pentahydrate as bismuth source, and calcium acetate as pore-forming agent. Then, iron ferricyanide nanocubes are prepared with K3Fe(CN)6 and Na2S2O3 as sodium ion intercalation electrode materials.

[0039] The specific preparation steps are as follows:

[0040] Add 2 g of agar powder and 1.5 g of calcium acetate to 90 mL of deionized water, and stir magnetically in a 95 ℃ water bath for 30 min. The resulting solution is denoted as Solution 1. Place 2 mmol of bismuth nitrate pentahydrate in a beaker, add 10 mL of acetic acid solution, and stir magnetically to dissolve the bismuth nitrate. This solution is denoted as Solution 2. Pour Solution 2 into Solution 1, stir in a 50 ℃ water bath for 1 h, and then dry in a 50 ℃ oven for 48 h. The dried precursor is carbonized in a N2 atmosphere for 1 h at a carbonization temperature of 800 ℃ and a heating rate of 10 ℃ / min. The carbonized sample is then placed in a 0.03 mol / L dilute hydrochloric acid solution to remove the template agent. After washing several times with deionized water, the filtrate is neutralized. Finally, the residue is dried at 60 ℃ to obtain the final product, denoted as BiOCl@MC.

[0041] The preparation steps of ferricyanide nanocubes are as follows: 2 mmol K3Fe(CN)6 and 4 mmol Na2S2O3 were weighed and dissolved in 20 mL deionized water at room temperature. The mixture was magnetically stirred in a water bath at 60 °C for 48 h, then centrifuged at 4000 rpm for 10 min. The solid product was washed with deionized water several times and then vacuum dried at 120 °C for 12 h to finally obtain FeFe(CN)6 nanocubes. Example 2

[0042] Step 1: Take 1L of fermentation water from the anaerobic fermentation of kitchen waste (ammonia nitrogen content 900mg / L, COD value 460mg / L, sodium chloride concentration 8.3g / L). The electrode material for electrochemical oxidation is ruthenium-iridium material, the temperature condition is 60℃ water bath heating, the electrochemical oxidation potential is 1.25V (VS. SCE), and the electrolysis time is 20h. The ammonia nitrogen content after electrochemical oxidation was measured to be 0mg / L and the COD value was 75.4mg / L, with a COD conversion rate of 82.9%, using the ammonia nitrogen sodium reagent method and a COD digestion tester.

[0043] Step 2: Add a mixed catalyst to the liquid after electro-oxidation in Step 1 at a NiO:Fe2O3 mass ratio of 1:15 and a solid-liquid mass ratio of 1:25, and apply the catalyst at 500 W / m 2 The conversion rate of sodium hypochlorite was 98.4% after decomposition under light for 10 hours.

[0044] Step 3: A capacitor was constructed using a double-layer adsorption-coated BiOCl@MC material with a mass ratio of 10:9 and sodium ion intercalation electrode material made of ferricyanide nanocubes. After multiple adsorption / desorption processes via capacitive deionization, the sodium chloride concentration in the biogas slurry was reduced to 0.03 g / L. The BiOCl@MC material and ferricyanide nanocubes were prepared in the same manner as in Example 1.

[0045] Step 4: The capacitor that adsorbed sodium chloride was discharged in the sodium chloride storage tank to remove sodium chloride. After the discharge, the capacitor was digested and the sodium chloride concentration was measured to be 0 mg / L. The discharged capacitor was then returned to Step 3 for recycling until the sodium chloride content in the solution met the discharge standard. The sodium chloride storage tank contained a sodium chloride solution with a concentration of 4.6 mol / L at 15-25℃. The sodium chloride storage tank was then subjected to MVR evaporation and concentration, requiring 11% of the original water sample volume to be evaporated. Example 3

[0046] Step 1: Take 1L of ultrafiltration wastewater from the anaerobic fermentation of kitchen waste (ammonia nitrogen content 790mg / L, COD value 340mg / L, sodium chloride concentration 11.2g / L). Use ruthenium-iridium electrodes for electrochemical oxidation, with a 40℃ water bath heating temperature, an electrochemical oxidation potential of 1.20V (VS. SCE), and an electrolysis time of 20h. The ammonia nitrogen content after electrochemical oxidation was measured to be 0mg / L and the COD value to be 20.3mg / L using the sodium ammonia nitrogen reagent method and a COD digestion analyzer, resulting in a COD conversion rate of 94.1%.

[0047] Step 2: Add a mixed catalyst to the liquid after electro-oxidation in Step 1 at a NiO:Fe2O3 mass ratio of 1:10 and a solid-liquid mass ratio of 1:25, and apply the catalyst at 500 W / m 2The conversion rate of sodium hypochlorite was 95.2% after decomposition under light conditions for 10 hours.

[0048] Step 3: A capacitor was constructed using a double-layer adsorption-coated BiOCl@MC material with a mass ratio of 10:9 and sodium ion intercalation electrode material made of ferricyanide nanocubes. After multiple adsorption / desorption processes via capacitive deionization, the sodium chloride concentration in the biogas slurry was reduced to 0.1 g / L. The BiOCl@MC material and ferricyanide nanocubes were prepared in the same manner as in Example 1.

[0049] Step 4: The capacitor that adsorbed sodium chloride was discharged in the sodium chloride storage tank to remove sodium chloride. After the discharge, the capacitor was digested and the sodium chloride concentration was measured to be 0 mg / L. The discharged capacitor was then returned to Step 3 for recycling until the sodium chloride content in the solution met the discharge standard. The sodium chloride storage tank contained a sodium chloride solution with a concentration of 4.6 mol / L at 15-25℃. The sodium chloride storage tank was then subjected to MVR evaporation and concentration, requiring 10.4% of the original water sample volume to be evaporated. Example 4

[0050] Step 1: Take 1L of ultrafiltration wastewater from the anaerobic fermentation of kitchen waste (ammonia nitrogen content 790mg / L, COD value 265mg / L, sodium chloride concentration 12.7g / L). Use ruthenium-iridium electrodes for electrochemical oxidation, with a 50℃ water bath heating temperature, an electrochemical oxidation potential of 1.15V (VS. SCE), and an electrolysis time of 20h. The ammonia nitrogen content after electrochemical oxidation was measured to be 0mg / L and the COD content to be 13.2mg / L using the ammonia nitrogen sodium reagent method and a COD digestion analyzer, resulting in a COD conversion rate of 95.0%.

[0051] Step 2: Add a mixed catalyst to the liquid after electro-oxidation in Step 1 at a NiO:Fe2O3 mass ratio of 1:25 and a solid-liquid mass ratio of 1:30, and apply the catalyst at 600 W / m 2 The conversion rate of sodium hypochlorite was 97.2% after decomposition under light for 10 hours.

[0052] Step 3: A capacitor was constructed using a double-layer adsorption-coated BiOCl@MC material with a mass ratio of 10:9 and sodium ion intercalation electrode material made of ferricyanide nanocubes. After multiple adsorption / desorption processes via capacitive deionization, the sodium chloride concentration in the biogas slurry was reduced to 0.1 g / L. The BiOCl@MC material and ferricyanide nanocubes were prepared in the same manner as in Example 1.

[0053] Step 4: The capacitor that adsorbed sodium chloride was discharged in the sodium chloride storage tank to desorb the sodium chloride. After the desorption was completed, the sodium chloride concentration of the capacitor was measured to be 0 mg / L. The discharged capacitor was then returned to Step 3 for recycling until the sodium chloride content in the solution met the discharge standard. The sodium chloride storage tank contained a sodium chloride solution with a concentration of 4.6 mol / L at 15-25℃. The sodium chloride storage tank was then subjected to MVR evaporation and concentration, requiring 10.7% of the original water sample volume to be evaporated. Example 5

[0054] Step 1: Take 1L of reverse osmosis concentrate from the anaerobic fermentation slurry of kitchen waste (ammonia nitrogen content 1000mg / L, COD value 820mg / L, sodium chloride concentration 35.4g / L). The electrode material for electrochemical oxidation is ruthenium-iridium material, the temperature condition is 60℃ water bath heating, the electrochemical oxidation potential is 1.05V (VS. SCE), and the electrolysis time is 20h. The ammonia nitrogen content and COD value after electrochemical oxidation are both 0mg / L, as measured by the ammonia nitrogen sodium reagent method and COD digestion tester.

[0055] Step 2: Add a mixed catalyst to the liquid obtained from the electro-oxidation in Step 1 at a NiO:Fe2O3 mass ratio of 1:21 and a solid-liquid mass ratio of 1:40, and apply the catalyst at 600 W / m 2 The conversion rate of sodium hypochlorite was measured to be 83.7% after decomposition under light conditions for 5 hours.

[0056] Step 3: A capacitor was constructed using a double-layer adsorption-coated BiOCl material with a mass ratio of 10:9 and an iron sodium ferricyanide ion intercalation electrode material. After multiple adsorption / desorption processes using the capacitor deionization method, the sodium chloride concentration in the biogas slurry was reduced to 0.1 g / L.

[0057] Step 4: The capacitor that adsorbed sodium chloride was discharged in the sodium chloride storage tank to remove sodium chloride. After the discharge, the capacitor was digested and the sodium chloride concentration was measured to be 0 mg / L. The discharged capacitor was then returned to Step 3 for recycling until the sodium chloride content in the solution met the discharge standard. The sodium chloride storage tank contained a sodium chloride solution with a concentration of 4.6 mol / L at 15-25℃. The sodium chloride storage tank was then subjected to MVR evaporation and concentration, requiring 11.3% of the original water sample volume to be evaporated. Example 6

[0058] Step 1: Take 1L of reverse osmosis concentrate from the anaerobic fermentation slurry of kitchen waste (ammonia nitrogen content 1000mg / L, COD value 820mg / L, sodium chloride concentration 35.4g / L). The electrode material for electrochemical oxidation is ruthenium-iridium material, the temperature condition is 40℃ water bath heating, the electrochemical oxidation potential is 1.05V (VS. SCE), and the electrolysis time is 20h. The ammonia nitrogen content and COD value after electrochemical oxidation are both 0mg / L, as measured by the ammonia nitrogen sodium reagent method and COD digestion tester.

[0059] Step 2: Add a mixed catalyst to the liquid after electro-oxidation in Step 1 at a NiO:Fe2O3 mass ratio of 1:17 and a solid-liquid mass ratio of 1:30, and apply the catalyst at 700 W / m 2 The conversion rate of sodium hypochlorite was 91.8% after decomposition under light for 10 hours.

[0060] Step 3: A capacitor was constructed using a double-layer adsorption-coated BiOCl@MC material with a mass ratio of 10:9 and a Prussian blue electrode material. After multiple adsorption / desorption processes via capacitive deionization, the sodium chloride concentration in the biogas slurry was reduced to 0.6 g / L. The BiOCl@MC material was prepared in the same manner as in Example 1.

[0061] Step 4: The capacitor that adsorbed sodium chloride was discharged in the sodium chloride storage tank to remove sodium chloride. After the discharge, the capacitor was digested and the sodium chloride concentration was measured to be 0 mg / L. The discharged capacitor was then returned to Step 3 for recycling until the sodium chloride content in the solution met the discharge standard. The sodium chloride storage tank contained a sodium chloride solution with a concentration of 4.6 mol / L at 15-25℃. The sodium chloride storage tank was then subjected to MVR evaporation and concentration, requiring 10.5% of the original water sample volume to be evaporated.

[0062] It should be noted that, in this document, relational terms such as "first" and "second" are used only to distinguish one entity or operation from another, and do not necessarily require or imply any such actual relationship or order between these entities or operations. Furthermore, the terms "comprising," "including," or any other variations thereof are intended to cover non-exclusive inclusion, such that a process, method, article, or apparatus that comprises a list of elements includes not only those elements but also other elements not expressly listed, or elements inherent to such process, method, article, or apparatus.

[0063] It should be noted that the above content merely illustrates the technical concept of the present invention and should not be construed as limiting the scope of protection of the present invention. For those skilled in the art, various improvements and modifications can be made without departing from the principle of the present invention, and all such improvements and modifications fall within the scope of protection of the claims of the present invention.

Claims

1. A method for electrochemically treating anaerobic fermentation biogas slurry from kitchen waste, characterized in that, It mainly includes the following steps; Step 1: Obtain the anaerobic fermentation slurry of kitchen waste by electrochemical oxidation treatment; Step 2: Reduce the remaining hypochlorite ions in the biogas slurry after electro-oxidation to chloride ions by chlorate decomposition method to obtain the decomposed biogas slurry; Step 3: Construct a capacitor using chloride ion adsorption material and sodium ion intercalation electrode material, and adsorb sodium chloride in the decomposed biogas slurry by capacitive deionization method; Step 4: Discharge the capacitor that has adsorbed sodium chloride in the sodium chloride storage tank to desorb the sodium chloride. After discharge, return the capacitor to Step 3 to adsorb sodium chloride again. Repeat this process multiple times until the sodium chloride content in the biogas slurry meets the discharge standard. In step three, the chloride ion adsorption material includes an electric double layer adsorption material and a chloride ion conversion material; the sodium ion intercalation electrode material includes an electric double layer electrode material and a pseudocapacitive electrode material; the electric double layer electrode material is one or more of activated carbon, carbon fiber, carbon gel, and carbon nanotubes; the pseudocapacitive electrode material is one or more of graphite, Prussian blue, Prussian white, and ferric ferricyanide; and the chloride ion adsorption material is one or more of Ag composite material, Bi composite material, and Fe composite material. In step four, the concentration of the sodium chloride solution in the sodium chloride storage tank at 15-25℃ is 4.6 mol / L.

2. The method for electrochemically treating anaerobic fermentation biogas slurry from kitchen waste according to claim 1, characterized in that, In step one, the electrode material for the electrochemical oxidation is ruthenium-iridium material, and the temperature is 30℃-60℃.

3. The method for electrochemical treatment of anaerobic fermentation biogas slurry from kitchen waste according to claim 1, characterized in that, In step one, the electrochemical oxidation site is 1.05V-1.25V, and the electrolysis time is 20h.

4. The method for electrochemical treatment of anaerobic fermentation biogas slurry from kitchen waste according to claim 1, characterized in that, In step two, the chlorate decomposition method is one or more of the following: thermal decomposition, photodecomposition, and catalytic decomposition.

5. The method for electrochemically treating anaerobic fermentation biogas slurry from kitchen waste according to claim 4, characterized in that, The catalyst used in the catalytic decomposition method is one or more of nickel oxide, cobalt oxide, copper oxide, and iron oxide; the mass ratio of the catalyst to the biogas slurry after electro-oxidation is 1:25-40.

6. The method for electrochemically treating anaerobic fermentation biogas slurry from kitchen waste according to claim 4, characterized in that, The photolysis method is performed at 300-800 W / m 2 Decomposes under light conditions.

7. The method for electrochemically treating anaerobic fermentation biogas slurry from kitchen waste according to claim 4, characterized in that, The thermal decomposition method involves raising the temperature of the biogas slurry after electro-oxidation to 40-60℃.

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