CN111807576A - Method for treating domestic garbage leachate by using domestic garbage incineration fly ash - Google Patents
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Abstract
The invention discloses a method for treating domestic garbage leachate by using domestic garbage incineration fly ash, which comprises the steps of adding a hydrochloric acid aqueous solution into the domestic garbage leachate; respectively weighing water and the fly ash from the incineration of the household garbage, mixing, stirring and centrifuging to perform solid-liquid separation to obtain a water washing solution of the fly ash from the incineration of the household garbage and solid slurry of the fly ash; performing electric treatment on the domestic garbage incineration fly ash water washing liquid, trapping gas generated by an electric anode chamber, directly introducing the gas into acidified domestic garbage leachate, and aerating the domestic garbage leachate; scraping and filtering the domestic garbage leachate to obtain oily nitrogen trichloride and denitrification leachate; weighing the iron-aluminum agent and the fly ash solid slurry, and drying in vacuum to obtain fly ash purification powder; and (3) weighing the denitrification leachate and the fly ash purification powder, mixing, stirring and carrying out solid-liquid separation to obtain the domestic garbage leachate purification liquid and the gelled fly ash solid slurry. The method can recover 86 percent of nitrogen trichloride at most and remove 98 percent of ammonia nitrogen, 97 percent of COD, 98 percent of total phosphorus and 98 percent of mercury in the landfill leachate.
Description
Technical Field
The invention relates to the field of harmless treatment of hazardous wastes, in particular to a method for treating domestic garbage leachate by using domestic garbage incineration fly ash, and particularly relates to a method for recovering nitrogen trichloride from the domestic garbage leachate and realizing purification of the domestic garbage leachate.
Background
Household garbage under a landfill is in an anaerobic and humid environment and is continuously affected by biological and chemical degradation. In addition, surface water invasion and underground water infiltration enable high-concentration organic and inorganic pollutants in the household garbage to be transferred into a liquid state, and household garbage leachate is formed. The components of the domestic garbage leachate are very complex, and if the domestic garbage leachate is not treated for a long time, the domestic garbage leachate is easy to cause serious pollution to the surrounding water and soil environment and bring harm to the health of residents.
The existing disposal methods of landfill leachate mainly comprise a membrane treatment method, a chemical oxidation method, a photoelectric catalysis method, an adsorption method, a biological method and the like. Compared with other methods, the application of the adsorption method to treat the domestic garbage leachate has the characteristics of simple operation, controllable treatment time, wide industrial popularization prospect and the like. However, the application and popularization of the adsorption method in the treatment of the domestic garbage leachate are restricted by the problems that the preparation of the adsorbent is complicated, the performance of the adsorbent is poor, the post-treatment links of the used adsorbent are more and the like.
The fly ash from the incineration of the household garbage has larger specific surface area and certain adsorbability and gelatinization. However, the fly ash from incineration of household garbage belongs to dangerous waste, and not only contains heavy metal pollutants, but also has high chlorine content, which can reach 5% -25%.
Therefore, the treatment of the domestic waste leachate by using the domestic waste incineration fly ash needs to effectively utilize chloride ions in the fly ash, effectively utilize the gelling property of the fly ash and solve the problem of recycling the fly ash after use.
Disclosure of Invention
The purpose of the invention is as follows: the invention aims to solve the technical problem of providing a method for treating domestic garbage leachate by using domestic garbage incineration fly ash.
The technical scheme is as follows: in order to solve the technical problems, the invention adopts the following technical scheme: a method for disposing domestic garbage leachate by using domestic garbage incineration fly ash comprises the following steps:
1) adding a hydrochloric acid aqueous solution into the domestic garbage leachate to ensure that the pH value is 2.5-4.5, so as to obtain acidified domestic garbage leachate;
2) respectively weighing water and the household garbage incineration fly ash, mixing, stirring for 0.5-1.5 hours, and centrifuging to perform solid-liquid separation to obtain household garbage incineration fly ash water washing liquid and fly ash solid slurry;
3) performing electric treatment on the domestic garbage incineration fly ash water washing liquid in an electric device, synchronously trapping gas generated in an anode chamber of the electric device and directly introducing the gas into acidified domestic garbage leachate through an aeration pump, wherein the electric treatment of the domestic garbage incineration fly ash water washing liquid and the aeration of the domestic garbage leachate are performed simultaneously; wherein the gas in the anode chamber is a mixed gas of oxygen and chlorine, the oxygen is generated by electrolyzing water in the anode, and the chlorine is obtained by migrating chloride ions to the surface of the anode and losing electron oxidation;
4) scraping the oily nitrogen trichloride out of the domestic garbage leachate by using a scraper to obtain the oily nitrogen trichloride and the denitrification leachate;
5) weighing the iron-aluminum agent and the fly ash solid slurry, mixing, continuously stirring for 0.5-1.5 hours under a sealed condition, and performing vacuum drying to obtain fly ash purification powder;
6) and respectively weighing the denitrification leachate and the fly ash purification powder, mixing, stirring for 0.5-1.5 hours, and carrying out solid-liquid separation to obtain the domestic garbage leachate purification solution and the gelled fly ash solid slurry.
The electric treatment, also called electric restoration, refers to that chloride ions in the domestic waste incineration fly ash water washing liquid move to the surface of the anode under the action of electromigration and lose electrons to be converted into chlorine, and meanwhile, the surface of the anode electrode is hydrolyzed to generate oxygen.
Wherein the mass fraction of hydrochloric acid in the hydrochloric acid aqueous solution in the step 1) is 5-20%.
Wherein the liquid-solid ratio of the water and the domestic garbage incineration fly ash in the step 2) is 1-4: 1 mL/mg.
And 3) adopting a direct current power supply as an electric power supply, wherein the electric voltage gradient is 0.5-2.5V/cm.
The iron-aluminum agent in the step 5) is obtained by mixing ferrous sulfate and aluminum sulfate, and the molar ratio of ferrous iron in the ferrous sulfate to trivalent aluminum in the aluminum sulfate is 2-4: 1.
Wherein, the mass ratio of the iron-aluminum agent and the fly ash solid slurry in the step 5) is 5-15: 100.
Wherein, the liquid-solid ratio of the deamination percolate and the fly ash purification powder in the step 6) is 2-10: 1 mL/mg.
The working principle of the invention is as follows: the adjustment of the domestic waste leachate with hydrochloric acid can convert part of the ammonium salts in the leachate into ammonium chloride. After the domestic waste incineration fly ash is mixed with water, a large amount of chloride ions are transferred into fly ash water washing liquid in the stirring process. In the electrokinetic process, chloride ions move to the surface of the anode by electromigration and lose electrons to chlorine gas. Meanwhile, the surface of the anode electrode is hydrolyzed to generate oxygen. The mixed gas of oxygen and chlorine is captured and aerated into the acidified domestic garbage incineration percolate, and ammonium chloride can be converted into nitrogen trichloride through the oxidation effect of the chlorine. Meanwhile, chlorine and water react to generate hypochlorous acid, and the hypochlorous acid further oxidizes ammonium salts to convert the ammonium salts into nitrogen, water and chloride ions. The chloride ions circularly participate in the generation process of the nitrogen trichloride. Meanwhile, chlorine and hypochlorous acid can oxidize small molecular organic matters in the landfill leachate, so that the small molecular organic matters are mineralized to generate carbon dioxide and water. Carbon dioxide is removed from the leachate along with oxygen. After the iron-aluminum agent is mixed with the fly ash solid slurry, ferrous ions and aluminum ions are adsorbed on the surfaces of the fly ash particles after water washing and react with hydroxyl in the pore liquid of the fly ash solid slurry to generate layered mixed iron-aluminum hydroxide. After the deamination leachate and the fly ash purification powder are mixed, phosphorus pollutants, residual organic pollutants and heavy metal pollutants in the leachate can be quickly adsorbed onto the mixed iron-aluminum hydroxide loaded by the fly ash particles in the stirring process, so that the purification of the landfill leachate is realized.
Has the advantages that: the method has simple process, and can convert ammonia nitrogen in the garbage percolate into nitrogen trichloride and realize the degradation of partial organic pollutants by utilizing the mixed gas generated in the electric treatment process of the municipal solid waste incineration fly ash. The fly ash after the electric treatment is converted into an adsorption material, so that the purification of the landfill leachate is further realized. The method can recover 86 percent of nitrogen trichloride at most and remove 98 percent of ammonia nitrogen, 97 percent of COD, 98 percent of total phosphorus and 98 percent of mercury in the landfill leachate. The gelled fly ash solid slurry obtained by the invention can also be used for preparing sintered ceramsite, and the leaching concentration of the heavy metal of the prepared ceramsite is lower than the pollution control standard of a domestic garbage landfill.
Drawings
FIG. 1 is a flow chart of the present invention.
Fig. 2 is a schematic view of the electric device of the present invention.
Detailed Description
The invention is further described below with reference to the figures and examples.
In the embodiment, the sampling and basic property explanation of the domestic garbage leachate are as follows: the landfill leachate for the test is taken from a sanitary landfill of domestic garbage in the Qingcheng mountain of the Haizhou area of the Hongyun harbor city. The COD mass concentration of the urban domestic garbage percolate of the batch is 1049mg/L, the total phosphorus concentration is 164mg/L, the ammonia nitrogen concentration is 786mg/L, and the mercury ion concentration is 0.74 mg/L.
The household garbage incineration fly ash is taken from a certain garbage incineration power plant in Chongqing and collected by a bag-type dust collector. The waste incineration fly ash sample contains 33.7439% of Ca, 32.5362% of O, 16.6467% of C1, 4.8491% of Na, 3.6348% of K, 2.4572% of S, 1.9651% of Si, 1.1437% of Mg, 0.9634% of Fe, 0.5287% of Zn, 0.5044% of Al, 0.3246% of P, 0.2743% of Ti, 0.1987% of Pb, 0.0945% of Br, 0.0547% of Cu, 0.0468% of Cd and 0.0332% of Mn.
Example 1 influence of pH of domestic waste leachate on recovery rate of nitrogen trichloride and purification effect of domestic waste leachate
And adding a hydrochloric acid aqueous solution into the domestic garbage percolate to ensure that the pH values are respectively 1, 1.5, 2, 2.5, 3.5, 4.5, 5, 5.5 and 6, thus obtaining nine groups of acidified domestic garbage percolate, wherein the mass fraction of hydrochloric acid in the hydrochloric acid aqueous solution is 5%. Respectively weighing water and the domestic garbage incineration fly ash according to the liquid-solid ratio of 1: 1mL/mg of the water to the domestic garbage incineration fly ash, mixing, stirring for 0.5 hour, and centrifuging to perform solid-liquid separation to obtain nine groups of domestic garbage incineration fly ash water washing liquids and nine groups of fly ash solid slurry. Nine groups of domestic waste incineration fly ash water washing liquids are added into a sample treatment area of an electric device in the figure 2 for electric treatment, gas generated in an anode chamber in the electric device is synchronously collected and is respectively and directly introduced into nine groups of acidified domestic waste leachate through an aeration pump, wherein a power supply of the electric device adopts a direct current power supply, the voltage gradient of the electric device is 0.5V/cm, and the electric treatment of the domestic waste incineration fly ash and the aeration of the domestic waste leachate are simultaneously carried out. Subsequently, the oily nitrogen trichloride is scraped out of the nine groups of domestic garbage leachate by a scraper, so that nine groups of oily nitrogen trichloride and nine groups of denitrification leachate are obtained. Ferrous sulfate and aluminum sulfate are respectively weighed according to the molar ratio of ferrous iron to trivalent aluminum of 2: 1 and mixed to obtain the ferro-aluminum agent. Nine groups of iron-aluminum agents and the nine groups of fly ash solid-state slurries are respectively weighed according to the mass ratio of the iron-aluminum agents to the fly ash solid-state slurries of 5:100, mixed, continuously stirred for 0.5 hour under the sealing condition and dried in vacuum, and nine groups of fly ash purification powders are obtained. Respectively weighing the denitrification leachate and the fly ash purification powder according to the liquid-solid ratio of the deamination leachate to the fly ash purification powder of 2: 1mL/mg, mixing, stirring for 0.5 hour, and carrying out solid-liquid separation to obtain nine groups of domestic garbage leachate purification solutions and nine groups of gelled fly ash solid slurries.
Detecting the ammonia nitrogen concentration and calculating the ammonia nitrogen removal rate: the concentration of the ammonia nitrogen in the domestic garbage leachate is measured according to salicylic acid spectrophotometry for measuring the ammonia nitrogen in water (HJ 536-2009). The ammonia nitrogen removal rate is calculated according to the formula (1), wherein RNFor ammonia nitrogen removal, cNOIs the initial concentration (mg/L) of ammonia nitrogen in the percolate before treatment, cNtThe residual concentration (mg/L) of ammonia nitrogen in the treated percolate is obtained.
And (3) measuring the molar quantity of the nitrogen trichloride and calculating the recovery rate of the nitrogen trichloride: the molar amount of nitrogen trichloride can be measured in accordance with Standard test method for measuring Nitrogen trichloride in liquid chlorine by High Performance Liquid Chromatography (HPLC) (ASTM E2036-2007). The recovery of nitrogen trichloride is calculated according to the formula (2), wherein LNFor nitrogen trichloride recovery, MN0Molar amount of nitrogen trichloride recovered after the test, cN0Is the initial concentration (mg/L) of ammonia nitrogen in the percolate before treatment, cN0Is the initial concentration (mg/L), V, of ammonia nitrogen in the percolate before treatment0Is the volume of leachate before disposal.
COD concentration detection and COD removal rate calculation: the chemical oxygen demand COD concentration of the domestic garbage leachate is measured according to the national standard bichromate method for measuring the chemical oxygen demand of water (GB 11914-. The COD removal rate was calculated according to the formula (3) where RCODAs the removal rate of COD, c0And ctThe COD concentration (mg/L) of the domestic garbage percolate before and after treatment is respectively.
Detection of total phosphorus concentration and removal of total phosphorusAnd (3) calculating a division rate: the total phosphorus concentration of the domestic garbage leachate is measured according to the standard continuous flow-ammonium molybdate spectrophotometry for measuring water quality phosphate and total phosphorus (HJ 670-2013). The total phosphorus removal was calculated according to formula (4), where RTPAs a total phosphorus removal rate, cTPOAnd cTPtThe total phosphorus concentration (mg/L) of the domestic garbage leachate before and after treatment is respectively.
Mercury ion concentration detection and removal rate calculation: the concentration of mercury ions in the domestic garbage leachate is measured according to the atomic fluorescence method for measuring mercury, arsenic, selenium, bismuth and antimony in water (HJ 695-. The mercury ion removal rate is calculated according to formula (5), wherein RHAs mercury ion removal rate, cH0Is the initial concentration (mg/L) of mercury ions in the percolate before treatment, cHtThe concentration of mercury ions in the treated leachate (mg/L) is shown.
The results of COD, total phosphorus, ammonia nitrogen, mercury ion removal rate and nitrogen trichloride recovery rate are shown in Table 1.
TABLE 1 influence of pH of domestic waste leachate on recovery of nitrogen trichloride and purification effect of domestic waste leachate
As can be seen from table 1, when the pH of the domestic landfill leachate is less than 2.5 (as shown in table 1, when the pH of the domestic landfill leachate is 2, 1.5, 1 and lower values not listed in table 1), hydrogen ions in the landfill leachate are excessive, hypochlorous acid generated after chlorine is dissolved in water is reduced, the oxidation efficiency of chlorine is reduced, and mercury ions and hydrogen ions have enhanced adsorption competition, so that the recovery rate of nitrogen trichloride and the removal rate of ammonia nitrogen, COD, total phosphorus and mercury ions in leachate pollutants are all significantly reduced along with the reduction of the pH of the domestic landfill leachate. When the pH value of the domestic garbage leachate is equal to 2.5-4.5 (as shown in table 1, when the pH value of the domestic garbage leachate is 2.5, 3.5 or 4.5), the mixed gas of oxygen and chlorine is captured and exposed into the acidified domestic garbage incineration leachate, and ammonium chloride can be converted into nitrogen trichloride through the oxidation effect of the chlorine. Meanwhile, chlorine and water react to generate hypochlorous acid, and the hypochlorous acid further oxidizes ammonium salts to convert the ammonium salts into nitrogen, water and chloride ions. The chloride ions circularly participate in the generation process of the nitrogen trichloride. Meanwhile, chlorine and hypochlorous acid can oxidize small molecular organic matters in the landfill leachate, so that the small molecular organic matters are mineralized to generate carbon dioxide and water. Carbon dioxide is removed from the leachate along with oxygen. Finally, the recovery rate of nitrogen trichloride is more than 76%, the ammonia nitrogen content of the percolate pollutant is more than 89%, the COD removal rate is more than 87%, the total phosphorus removal rate is more than 91%, and the mercury removal rate is more than 93%. When the pH of the domestic landfill leachate is greater than 4.5 (as shown in table 1, when the pH of the domestic landfill leachate is 5, 5.5, 6 and higher values not listed in table 1), the addition amount of hydrochloric acid is too small, the generation amount of ammonium chloride is reduced, the generation amount of nitrogen trichloride is reduced, so that the recovery rate of nitrogen trichloride is remarkably reduced along with the further increase of the pH of the domestic landfill leachate, and the removal rates of leachate pollutants, ammonia nitrogen, COD, total phosphorus and mercury ions are not remarkably changed along with the further increase of the pH of the domestic landfill leachate. Therefore, comprehensively, the benefit and the cost are combined, and when the pH value of the domestic garbage leachate is equal to 2.5-4.5, the recovery rate of the nitrogen trichloride and the purification effect of the domestic garbage leachate are improved most favorably.
Example 2 influence of the molar ratio of ferrous iron to ferric aluminum on the recovery of nitrogen trichloride and the purification effect of leachate of domestic garbage
And adding a hydrochloric acid aqueous solution into the domestic garbage percolate to enable the pH value to be 4.5, and obtaining the acidified domestic garbage percolate, wherein the mass fraction of hydrochloric acid in the hydrochloric acid aqueous solution is 12.5%. Respectively weighing water and the domestic garbage incineration fly ash according to the liquid-solid ratio of the water to the domestic garbage incineration fly ash of 2.5: 1mL/mg, mixing, stirring for 1 hour, and centrifuging to perform solid-liquid separation to obtain domestic garbage incineration fly ash water washing liquid and fly ash solid slurry. Adding the water washing liquid of the fly ash from the incineration of the household garbage into a sample treatment area of an electric device shown in figure 2 for electric treatment, synchronously capturing gas generated in an anode chamber of the electric device and directly introducing the gas into acidified household garbage leachate through an aeration pump, wherein a power supply of the electric device adopts a direct-current power supply, the voltage gradient of the electric device is 1.5V/cm, and the electric drive treatment of the fly ash from the incineration of the household garbage and the aeration of the household garbage leachate are carried out simultaneously. And then scraping the oily nitrogen trichloride out of the domestic garbage leachate by using a scraper to obtain the oily nitrogen trichloride and the denitrification leachate. Ferrous sulfate and aluminum sulfate are respectively weighed according to the molar ratio of ferrous iron to ferric aluminum of 0.5: 1, 1: 1, 1.5: 1, 2: 1, 3: 1, 4:1, 4.5: 1, 5:1 and 5.5: 1 and are mixed to obtain nine groups of iron-aluminum agents. Respectively weighing the Fe-Al agent and the fly ash solid slurry according to the mass ratio of the Fe-Al agent to the fly ash solid slurry of 10: 100, mixing, continuously stirring for 1 hour under a sealed condition, and drying in vacuum to obtain nine groups of fly ash purification powder. Respectively weighing the denitrification leachate and the fly ash purification powder according to the liquid-solid ratio of 6: 1mL/mg of the deamination leachate and the fly ash purification powder, mixing, stirring for 1 hour, and performing solid-liquid separation to obtain nine groups of domestic garbage leachate purification solutions and nine groups of gelled fly ash solid slurries.
The ammonia nitrogen concentration detection and ammonia nitrogen removal rate calculation, nitrogen trichloride molar quantity measurement and nitrogen trichloride recovery rate calculation, COD concentration detection and COD removal rate calculation, total phosphorus concentration detection and total phosphorus removal rate calculation, and mercury ion concentration detection and removal rate calculation are the same as those in example 1.
The results of COD, total phosphorus, ammonia nitrogen, mercury ion removal rate and nitrogen trichloride recovery rate are shown in Table 2.
TABLE 2 influence of the molar ratio of ferrous iron to ferric aluminum on the recovery of nitrogen trichloride and the purification effect of leachate of domestic garbage
As can be seen from table 2, when the molar ratio of the ferrous iron to the ferric aluminum is less than 2: 1 (as shown in table 2, when the molar ratio of the ferrous iron to the ferric aluminum is 1.5: 1, 1: 1, 0.5: 1 and lower ratios not listed in table 2), the ferrous ions are too small, the ferrous ions adsorbed on the surface of the fly ash particles after washing are reduced, so that the generation amount of the layered mixed iron-aluminum hydroxide is reduced, and the removal rates of ammonia nitrogen, COD, total phosphorus and mercury ions of leachate pollutants are all significantly reduced as the molar ratio of the ferrous iron to the ferric aluminum is reduced. When the molar ratio of the ferrous iron to the ferric aluminum is equal to 2-4: 1 (as shown in table 2, when the molar ratio of the ferrous iron to the ferric aluminum is 2: 1, 3: 1, or 4: 1), the ferrous ions and the aluminum ions are adsorbed on the surface of the fly ash particles after water washing and react with hydroxide radicals in pore liquid of the fly ash solid slurry to generate the layered mixed iron-aluminum hydroxide. After the deamination leachate and the fly ash purification powder are mixed, phosphorus pollutants, residual organic pollutants and heavy metal pollutants in the leachate can be quickly adsorbed onto the mixed iron-aluminum hydroxide loaded by the fly ash particles in the stirring process, so that the purification of the landfill leachate is realized. Finally, the recovery rate of nitrogen trichloride is more than 84%, the ammonia nitrogen content of the percolate pollutant is more than 93%, the COD removal rate is more than 92%, the total phosphorus removal rate is more than 94%, and the mercury removal rate is more than 96%. When the molar ratio of the ferrous iron to the ferric aluminum is greater than 4:1 (as shown in table 2, when the molar ratio of the ferrous iron to the ferric aluminum is 4.5: 1, 5:1, 5.5: 1 and higher ratios not listed in table 2), the ferrous iron is excessive, the ferrous hydroxide is excessive, the layered mixed iron-aluminum hydroxide is decreased, the adsorption sites of pollutants in the fly ash purification powder are decreased, and the removal rate of ammonia nitrogen, COD, total phosphorus and mercury ions in leachate pollutants is remarkably decreased as the molar ratio of the ferrous iron to the ferric aluminum is further increased. Therefore, in comprehensive terms, the benefit and the cost are combined, and when the molar ratio of the ferrous iron to the ferric aluminum is equal to 2-4: 1, the recovery rate of the nitrogen trichloride and the purification effect of the domestic garbage leachate are improved most favorably.
Example 3 influence of the mass ratio of Fe-Al agent to solid slurry of fly ash on the recovery rate of nitrogen trichloride and the purification effect of domestic garbage leachate
And adding a hydrochloric acid aqueous solution into the domestic garbage leachate to ensure that the pH value is 4.5, thereby obtaining the acidified domestic garbage leachate, wherein the mass fraction of hydrochloric acid in the hydrochloric acid aqueous solution is 20%. Respectively weighing water and the domestic garbage incineration fly ash according to the solid-to-liquid ratio of 4:1mL/mg of the water to the domestic garbage incineration fly ash, mixing, stirring for 1.5 hours, and centrifuging to perform solid-liquid separation to obtain domestic garbage incineration fly ash water washing liquid and fly ash solid slurry. Adding the domestic waste incineration fly ash washing liquid into a sample treatment area of an electric device shown in figure 2 for electric treatment, synchronously trapping gas generated in an anode chamber of the electric device and directly introducing the gas into acidified domestic waste leachate through an aeration pump, wherein a power supply of the electric device adopts a direct-current power supply, the voltage gradient of the electric device is 2.5V/cm, and the electric treatment of the domestic waste incineration fly ash and the aeration of the domestic waste leachate are carried out simultaneously. And then scraping the oily nitrogen trichloride out of the domestic garbage leachate by using a scraper to obtain the oily nitrogen trichloride and the denitrification leachate. Ferrous sulfate and aluminum sulfate are respectively weighed according to the molar ratio of ferrous iron to ferric aluminum of 4:1 and mixed to obtain the iron-aluminum agent. Weighing the Fe-Al agent and the fly ash solid slurry according to the mass ratio of the Fe-Al agent to the fly ash solid slurry of 2.5: 100, 3.5: 100, 4.5: 100, 5:100, 10: 100, 15:100, 15.5: 100, 16.5: 100 and 17.5: 100 respectively, mixing, continuously stirring for 1.5 hours under a sealed condition, and drying in vacuum to obtain nine groups of fly ash purification powder. Respectively weighing the denitrification leachate and the fly ash purification powder according to the liquid-solid ratio of 10:1mL/mg of the deamination leachate and the fly ash purification powder, mixing, stirring for 1.5 hours, and carrying out solid-liquid separation to obtain nine groups of domestic garbage leachate purification solutions and nine groups of gelled fly ash solid slurries.
The ammonia nitrogen concentration detection and ammonia nitrogen removal rate calculation, nitrogen trichloride molar quantity measurement and nitrogen trichloride recovery rate calculation, COD concentration detection and COD removal rate calculation, total phosphorus concentration detection and total phosphorus removal rate calculation, and mercury ion concentration detection and removal rate calculation are the same as those in example 1.
The results of COD, total phosphorus, ammonia nitrogen, mercury ion removal rate and nitrogen trichloride recovery rate are shown in Table 3.
Table 3 influence of the quality ratio of the solid-state slurry of the iron-aluminum agent and the fly ash on the recovery rate of the nitrogen trichloride and the purification effect of the domestic garbage percolate
As can be seen from table 3, when the mass ratio of the ferro-aluminum agent to the fly ash solid slurry is less than 5:100 (as shown in table 3, when the mass ratio of the ferro-aluminum agent to the fly ash solid slurry is 4.5: 100, 3.5: 100, 2.5: 100 and lower ratios not listed in table 3), the ferro-aluminum agent is less, and the ferrous ions and the aluminum ions adsorbed on the surface of the washed fly ash particles are less, so that the generation amount of the laminar mixed ferro-aluminum hydroxide is reduced, and the removal rate of ammonia nitrogen, COD, total phosphorus and mercury ions of leachate pollutants is significantly reduced as the mass ratio of the ferro-aluminum agent to the fly ash solid slurry is reduced. When the mass ratio of the ferro-aluminum agent to the fly ash solid slurry is 5-15: 100 (as shown in table 3, the mass ratio of the ferro-aluminum agent to the fly ash solid slurry is 5:100, 10: 100, 15: 100), after the ferro-aluminum agent and the fly ash solid slurry are mixed, ferrous ions and aluminum ions are adsorbed on the surface of the fly ash particles after water washing and react with hydroxide radicals in pore liquid of the fly ash solid slurry to generate layered mixed ferro-aluminum hydroxide. After the deamination leachate and the fly ash purification powder are mixed, phosphorus pollutants, residual organic pollutants and heavy metal pollutants in the leachate can be quickly adsorbed onto the mixed iron-aluminum hydroxide loaded by the fly ash particles in the stirring process, so that the purification of the landfill leachate is realized. Finally, the recovery rate of nitrogen trichloride is more than 86%, the ammonia nitrogen content of the percolate pollutant is more than 95%, the COD removal rate is more than 94%, the total phosphorus removal rate is more than 96%, and the mercury removal rate is more than 96%. When the mass ratio of the ferro-aluminum agent to the fly ash solid slurry is greater than 15:100 (as shown in table 3, when the mass ratio of the ferro-aluminum agent to the fly ash solid slurry is 15.5: 100, 16.5: 100, 17.5: 100 and higher ratios not listed in table 3), the removal rate of ammonia nitrogen, COD, total phosphorus and mercury ions of leachate pollutants is not obviously changed as the mass ratio of the ferro-aluminum agent to the fly ash solid slurry is further increased. Therefore, in a comprehensive aspect, the benefit and the cost are combined, and when the mass ratio of the iron-aluminum agent to the fly ash solid slurry is 5-15: 100, the nitrogen trichloride recovery rate and the purification effect of the domestic garbage leachate are improved most favorably.
Example 4 preparation of Haydite and detection of leaching Properties thereof
1. Preparing gelled fly ash solid slurry: and adding a hydrochloric acid aqueous solution into the domestic garbage leachate to ensure that the pH value is 4.5, thereby obtaining the acidified domestic garbage leachate, wherein the mass fraction of hydrochloric acid in the hydrochloric acid aqueous solution is 20%. Respectively weighing water and the domestic garbage incineration fly ash according to the solid-to-liquid ratio of 4:1mL/mg of the water to the domestic garbage incineration fly ash, mixing, stirring for 1.5 hours, and centrifuging to perform solid-liquid separation to obtain domestic garbage incineration fly ash water washing liquid and fly ash solid slurry. Adding the water washing liquid of the fly ash from the incineration of the household garbage into a sample treatment area of an electric device shown in figure 2 for electric treatment, synchronously trapping gas generated in an anode chamber of the electric device and directly introducing the gas into acidified household garbage leachate through an aeration pump, wherein a power supply of the electric device adopts a direct-current power supply, the voltage gradient of the electric device is 2.5V/cm, and the electric drive treatment of the fly ash from the incineration of the household garbage and the aeration of the household garbage leachate are carried out simultaneously. And then scraping the oily nitrogen trichloride out of the domestic garbage leachate by using a scraper to obtain the oily nitrogen trichloride and the denitrification leachate. Ferrous sulfate and aluminum sulfate are respectively weighed according to the molar ratio of ferrous iron to ferric aluminum of 4:1 and mixed to obtain the iron-aluminum agent. Respectively weighing the iron-aluminum agent and the fly ash solid slurry according to the mass ratio of the iron-aluminum agent to the fly ash solid slurry of 15:100, mixing, continuously stirring for 1.5 hours under a sealed condition, and drying in vacuum to obtain the fly ash purification powder. Respectively weighing the denitrification leachate and the fly ash purification powder according to the solid-to-liquid ratio of 10:1mL/mg of the deamination leachate and the fly ash purification powder, mixing, stirring for 1.5 hours, and performing solid-liquid separation to obtain the domestic garbage leachate purification liquid and the gelled fly ash solid slurry.
2. Preparing sintered ceramsite: drying the gelled fly ash solid slurry at the temperature of 105 ℃, grinding, and sieving by a 200-mesh sieve to obtain the gelled fly ash powder. Respectively weighing the diatomite and the gelling fly ash powder according to the mass ratio of 30: 100 of the diatomite to the gelling fly ash powder, mixing, granulating into balls by a granulator, and aging for 2 hours at room temperature to obtain the ceramsite to be sintered. And (2) placing the ceramsite to be sintered in a muffle furnace, setting the temperature rise range of room temperature to 1200 ℃, keeping the temperature rise rate at 50 ℃/min, continuously heating for 20 minutes at 1200 ℃, then stopping heating, and gradually cooling to room temperature to obtain the sintered ceramsite.
Leaching toxicity test: the ceramsite is crushed and sieved (4.75-9.50mm), and a leaching toxicity test is carried out according to an acetic acid buffer solution method (HJ/T299-2007) of a solid waste leaching toxicity leaching method. And determining the concentrations of heavy metal ions of Cu, Pb, Zn and Cd in the leaching solution by using a TAS-999 atomic absorption spectrophotometer. The mercury ion concentration was measured as in example 1. The test results are shown in Table 4.
TABLE 4 Haydite prepared from fly ash gelling agent and leaching toxicity (mg/L)
As can be seen from Table 4, the heavy metal leaching toxicity (mg/L) of the ceramsite prepared from the gelled fly ash powder is lower than the limit value of the concentration of the pollutants in the leachate specified in the Standard for pollution control of municipal solid waste landfill (GB 16889-2008).
Claims (7)
1. A method for disposing domestic garbage leachate by using domestic garbage incineration fly ash is characterized by comprising the following steps:
1) adding a hydrochloric acid aqueous solution into the domestic garbage leachate to ensure that the pH value is 2.5-4.5, so as to obtain acidified domestic garbage leachate;
2) respectively weighing water and the household garbage incineration fly ash, mixing, stirring for 0.5-1.5 hours, and centrifuging to perform solid-liquid separation to obtain household garbage incineration fly ash water washing liquid and fly ash solid slurry;
3) performing electric treatment on the domestic garbage incineration fly ash water washing liquid in an electric device, synchronously trapping gas generated in an anode chamber of the electric device and directly introducing the gas into acidified domestic garbage leachate through an aeration pump, wherein the electric treatment of the domestic garbage incineration fly ash water washing liquid and the aeration of the domestic garbage leachate are performed simultaneously;
4) scraping the oily nitrogen trichloride out of the domestic garbage leachate by using a scraper to obtain the oily nitrogen trichloride and the denitrification leachate;
5) weighing the iron-aluminum agent and the fly ash solid slurry, mixing, continuously stirring for 0.5-1.5 hours under a sealed condition, and performing vacuum drying to obtain fly ash purification powder;
6) and respectively weighing the denitrification leachate and the fly ash purification powder, mixing, stirring for 0.5-1.5 hours, and carrying out solid-liquid separation to obtain the domestic garbage leachate purification solution and the gelled fly ash solid slurry.
2. The method for treating household garbage leachate by using household garbage incineration fly ash according to claim 1, wherein the mass fraction of hydrochloric acid in the hydrochloric acid aqueous solution in the step 1) is 5% -20%.
3. The method for treating household garbage leachate by using household garbage incineration fly ash according to claim 1, wherein the liquid-solid ratio of the water and the household garbage incineration fly ash in the step 2) is 1-4: 1 mL/mg.
4. The method for treating leachate of domestic garbage with fly ash from incineration of domestic garbage according to claim 1, wherein the power source of the electric device in step 3) is a dc power source, and the voltage gradient of the electric device is 0.5-2.5V/cm.
5. The method for treating household garbage leachate by using household garbage incineration fly ash according to claim 1, wherein the iron-aluminum agent in the step 5) is obtained by mixing ferrous sulfate and aluminum sulfate, and the molar ratio of ferrous sulfate to trivalent aluminum of aluminum sulfate is 2-4: 1.
6. The method for treating household garbage leachate by using household garbage incineration fly ash according to claim 1, wherein the mass ratio of the iron-aluminum agent and the fly ash solid slurry in the step 5) is 5-15: 100.
7. The method for treating household garbage leachate by using household garbage incineration fly ash according to claim 1, wherein the liquid-solid ratio of the deamination leachate obtained in the step 6) to the fly ash purification powder is 2-10: 1 mL/mg.
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