CN114560595A - Treatment method and treatment system for kitchen waste biogas slurry - Google Patents

Treatment method and treatment system for kitchen waste biogas slurry Download PDF

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Publication number
CN114560595A
CN114560595A CN202210192275.4A CN202210192275A CN114560595A CN 114560595 A CN114560595 A CN 114560595A CN 202210192275 A CN202210192275 A CN 202210192275A CN 114560595 A CN114560595 A CN 114560595A
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reaction
anaerobic
tank
liquid
aerobic
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杨岸明
田盛
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BEIJING TANSI ENVIRONMENTAL PROTECTION TECHNOLOGYCO Ltd
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BEIJING TANSI ENVIRONMENTAL PROTECTION TECHNOLOGYCO Ltd
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    • C—CHEMISTRY; METALLURGY
    • C02—TREATMENT OF WATER, WASTE WATER, SEWAGE, OR SLUDGE
    • C02F—TREATMENT OF WATER, WASTE WATER, SEWAGE, OR SLUDGE
    • C02F9/00—Multistage treatment of water, waste water or sewage
    • C—CHEMISTRY; METALLURGY
    • C02—TREATMENT OF WATER, WASTE WATER, SEWAGE, OR SLUDGE
    • C02F—TREATMENT OF WATER, WASTE WATER, SEWAGE, OR SLUDGE
    • C02F1/00—Treatment of water, waste water, or sewage
    • C02F1/24—Treatment of water, waste water, or sewage by flotation
    • C—CHEMISTRY; METALLURGY
    • C02—TREATMENT OF WATER, WASTE WATER, SEWAGE, OR SLUDGE
    • C02F—TREATMENT OF WATER, WASTE WATER, SEWAGE, OR SLUDGE
    • C02F1/00—Treatment of water, waste water, or sewage
    • C02F1/52—Treatment of water, waste water, or sewage by flocculation or precipitation of suspended impurities
    • C—CHEMISTRY; METALLURGY
    • C02—TREATMENT OF WATER, WASTE WATER, SEWAGE, OR SLUDGE
    • C02F—TREATMENT OF WATER, WASTE WATER, SEWAGE, OR SLUDGE
    • C02F1/00—Treatment of water, waste water, or sewage
    • C02F2001/007—Processes including a sedimentation step
    • C—CHEMISTRY; METALLURGY
    • C02—TREATMENT OF WATER, WASTE WATER, SEWAGE, OR SLUDGE
    • C02F—TREATMENT OF WATER, WASTE WATER, SEWAGE, OR SLUDGE
    • C02F2301/00—General aspects of water treatment
    • C02F2301/08—Multistage treatments, e.g. repetition of the same process step under different conditions
    • C—CHEMISTRY; METALLURGY
    • C02—TREATMENT OF WATER, WASTE WATER, SEWAGE, OR SLUDGE
    • C02F—TREATMENT OF WATER, WASTE WATER, SEWAGE, OR SLUDGE
    • C02F3/00—Biological treatment of water, waste water, or sewage
    • C02F3/30—Aerobic and anaerobic processes
    • Y—GENERAL TAGGING OF NEW TECHNOLOGICAL DEVELOPMENTS; GENERAL TAGGING OF CROSS-SECTIONAL TECHNOLOGIES SPANNING OVER SEVERAL SECTIONS OF THE IPC; TECHNICAL SUBJECTS COVERED BY FORMER USPC CROSS-REFERENCE ART COLLECTIONS [XRACs] AND DIGESTS
    • Y02—TECHNOLOGIES OR APPLICATIONS FOR MITIGATION OR ADAPTATION AGAINST CLIMATE CHANGE
    • Y02W—CLIMATE CHANGE MITIGATION TECHNOLOGIES RELATED TO WASTEWATER TREATMENT OR WASTE MANAGEMENT
    • Y02W30/00—Technologies for solid waste management
    • Y02W30/20—Waste processing or separation

Abstract

The invention belongs to the technical field of solid waste treatment, and particularly relates to a treatment method and a treatment system for kitchen waste biogas slurry. The kitchen waste biogas slurry treatment method provided by the invention carries out pretreatment, advanced treatment and post-treatment on the basis of anaerobic ammonia oxidation treatment, solves the problem that the anaerobic ammonia oxidation process is difficult to start and operate due to high suspended matter, COD concentration and grease concentration of the kitchen waste biogas slurry, reduces the using amount and power consumption of water treatment agents by adopting the anaerobic ammonia oxidation treatment, simultaneously ensures the stability of the kitchen waste biogas slurry treatment effect, realizes the stable treatment of the kitchen waste biogas slurry, and ensures that the treated biogas slurry meets the discharge standard and has low treatment cost.

Description

Treatment method and treatment system for kitchen waste biogas slurry
Technical Field
The invention belongs to the technical field of solid waste treatment, and particularly relates to a treatment method and a treatment system for kitchen waste biogas slurry.
Background
With the rapid growth of economy in China, the consumption in catering is gradually increased, and a large amount of kitchen waste is generated. At present, the kitchen waste is generally subjected to unified recovery treatment, after renewable resources such as grease and the like are extracted from the kitchen waste, the generated solid matter still contains high-concentration organic matters which can be used as energy substances for recycling, the solid product obtained after the grease is extracted from the kitchen waste is generally subjected to full-mixing anaerobic fermentation, and biogas generated by fermentation is subjected to desulfurization and then generates power. And (3) performing solid-liquid separation on the slurry subjected to anaerobic fermentation, dehydrating to obtain biogas slurry and a final solid matter dry material, and transporting the final solid matter dry material to the outside, wherein the generated kitchen waste biogas slurry has the characteristics of high oil, high organic matter, high nitrogen and high solid, and can be discharged after further treatment.
At present, the treatment method for the kitchen waste biogas slurry is mainly a traditional nitrification and denitrification process, but the traditional process realizes removal of pollutants at the expense of high energy consumption and high material consumption, and has high treatment cost. The anaerobic ammonia oxidation process is the most advanced biological denitrification process in the world at present, and has the advantages of high denitrification load, low operation cost, no generation of excess sludge, greenhouse gas emission reduction and the like compared with the traditional biological denitrification process, but when the kitchen waste biogas slurry is treated by the anaerobic ammonia oxidation process, the anaerobic ammonia oxidation process is difficult to stabilize and treat due to the fact that the kitchen waste biogas slurry has the characteristics of high oil, high organic matters, high nitrogen, high solid and the like, the treatment effect is poor, and the treated wastewater cannot meet the emission standard.
Disclosure of Invention
In view of the above, the invention provides a treatment method and a treatment system for kitchen waste biogas slurry, the treatment method for kitchen waste biogas slurry provided by the invention can realize the stabilization treatment of the kitchen waste biogas slurry, and the treated biogas slurry meets the discharge standard and has low treatment cost.
In order to achieve the above object, the present invention provides the following technical solutions:
the invention provides a treatment method of kitchen waste biogas slurry, which comprises the following steps:
pretreating the kitchen waste biogas slurry to obtain a pretreatment solution, wherein the pretreatment comprises the steps of sequentially carrying out flotation, first anaerobic reaction, first aerobic reaction and first mud-water separation;
sequentially carrying out anaerobic ammoxidation reaction and second sludge-water separation on the pretreatment solution to obtain an anaerobic ammoxidation reaction clear solution, wherein the ammonia nitrogen content in the anaerobic ammoxidation reaction clear solution is less than 50mg/L, and the nitrate nitrogen content in the anaerobic ammoxidation reaction clear solution is less than 200 mg/L;
carrying out deep denitrification treatment on the anaerobic ammonia oxidation reaction clear solution to obtain deep denitrification treatment liquid, wherein the deep denitrification treatment comprises sequentially carrying out second aerobic reaction, second anaerobic reaction, third aerobic reaction and third sludge-water separation, the ammonia nitrogen content in the second aerobic reaction liquid obtained by the second aerobic reaction is less than 20mg/L, and the nitrate nitrogen content in the second anaerobic reaction liquid obtained by the second anaerobic reaction is less than 20 mg/L;
and carrying out post-treatment on the deep denitrification treatment liquid, wherein the post-treatment comprises flocculation and fourth sludge-water separation in sequence, and the total phosphorus content in the treated water obtained by the post-treatment is less than 5 mg/L.
Preferably, the dosage of the activated sludge for the first anaerobic reaction and the first aerobic reaction is 3000-5000 mg/L independently.
Preferably, when the anaerobic ammonia oxidation reaction is carried out, the dissolved oxygen content of the pretreatment solution is less than 0.5mg/L, the ammonia nitrogen content of the pretreatment solution is 700-900 mg/L, and the temperature of the pretreatment solution is 30-37 ℃.
Preferably, the kitchen waste biogas slurry is subjected to flotation to obtain flotation feed liquid;
the treatment method further comprises refluxing a part of the anaerobic ammonia oxidation reaction clear liquid to perform the first anaerobic reaction;
and the backflow flow of the anaerobic ammonia oxidation reaction clear liquid is 1-3 times of the flow of the flotation feed liquid.
Preferably, the first sludge-water separation further obtains first separated sludge, and the method further comprises refluxing a part of the first separated sludge to perform the first anaerobic reaction; and the reflux flow of the first separated sludge is the sum of the flow of the flotation solution and the reflux flow of the anaerobic ammonia oxidation reaction clear solution.
Preferably, the raw material for the second anaerobic reaction further comprises a carbon source, and the calculation formula of the adding amount of the carbon source is shown as formula 1:
the carbon source addition amount is 4 XQInflow water×(TN0-TNe) Carbon source COD equivalent formula 1;
in the formula 1, QInflow waterIs the flow rate of the second aerobic reaction liquid, TN0Total nitrogen content, TN, in the second aerobic reaction solutioneIs the total nitrogen content in the second anaerobic reaction liquid.
Preferably, the second sludge-water separation further obtains a second separated sludge, and the second separated sludge is refluxed to perform the anammox reaction.
Preferably, the third aerobic reaction is carried out to obtain a third aerobic reaction liquid;
the processing method further comprises the following steps: refluxing a part of the third aerobic reaction liquid to perform the second aerobic reaction;
and the reflux flow rate of the third aerobic reaction liquid is 1-3 times of the flow rate of the anaerobic ammonia oxidation reaction clear liquid for the second aerobic reaction.
Preferably, the third sludge-water separation also obtains third separated sludge;
the treatment method further comprises refluxing a portion of the third separated sludge for the second aerobic reaction; the reflux flow rate of the second separated sludge is the same as the flow rate of the anaerobic ammonia oxidation reaction clear liquid for carrying out the second aerobic reaction.
The invention provides a treatment system used in the treatment method of kitchen waste biogas slurry, which is characterized by comprising the following steps:
a flotation device 15, said flotation device 15 being provided with a liquid discharge;
the feeding hole of the first anaerobic tank 13 is communicated with the liquid discharging hole of the flotation equipment (15), and the first anaerobic tank 13 is also provided with a discharging hole;
a first aerobic tank 14 with a feed inlet communicated with a discharge outlet of the first anaerobic tank 13, wherein the first aerobic tank 14 is also provided with a discharge outlet;
a liquid inlet of the first sedimentation tank 110 is communicated with a liquid outlet of the first aerobic tank 14, and the first sedimentation tank 110 is also provided with a liquid outlet;
the feeding hole of the anaerobic ammonia oxidation reaction tank 23 is communicated with the liquid discharging hole of the first sedimentation tank 110, and the anaerobic ammonia oxidation reaction tank 23 is also provided with a discharging hole;
a liquid inlet of the second sedimentation tank 24 is communicated with a liquid outlet of the anaerobic ammonia oxidation reaction tank 23, and the second sedimentation tank 24 is also provided with a liquid outlet;
a second aerobic tank 31 with a feed inlet communicated with a liquid discharge outlet of the second sedimentation tank 24, wherein the second aerobic tank 31 is also provided with a discharge outlet;
a second anaerobic tank 33 with a feeding hole communicated with the discharging hole of the second aerobic tank 31, wherein the second anaerobic tank 33 is also provided with a discharging hole;
a third aerobic tank 34 with a feed inlet communicated with the discharge outlet of the second anaerobic tank 33, wherein the third aerobic tank 34 is also provided with a discharge outlet;
a liquid inlet of the third sedimentation tank 35 is communicated with a liquid outlet of the third aerobic tank 34, and the third sedimentation tank 35 is also provided with a liquid outlet;
the feed inlet is communicated with the liquid discharge port of the third sedimentation tank 35, and the flocculation device is also provided with a discharge port;
the liquid feed inlet with the fourth sedimentation tank 47 of flocculation device's discharge gate intercommunication, fourth sedimentation tank 47 still is provided with the liquid discharge gate.
The invention provides a treatment method of kitchen waste biogas slurry, which comprises the following steps: pretreating the kitchen waste biogas slurry to obtain a pretreatment solution, wherein the pretreatment comprises the steps of sequentially carrying out flotation, first anaerobic reaction, first aerobic reaction and first mud-water separation; sequentially carrying out anaerobic ammoxidation reaction and second sludge-water separation on the pretreatment solution to obtain an anaerobic ammoxidation reaction clear solution, wherein the ammonia nitrogen content in the anaerobic ammoxidation reaction clear solution is less than 50mg/L, and the nitrate nitrogen content in the anaerobic ammoxidation reaction clear solution is less than 200 mg/L; carrying out deep denitrification treatment on the anaerobic ammonia oxidation reaction clear solution to obtain deep denitrification treatment liquid, wherein the deep denitrification treatment comprises sequentially carrying out second aerobic reaction, second anaerobic reaction, third aerobic reaction and third sludge-water separation, the ammonia nitrogen content in the second aerobic reaction liquid obtained by the second aerobic reaction is less than 20mg/L, and the nitrate nitrogen content in the second anaerobic reaction liquid obtained by the second anaerobic reaction is less than 20 mg/L; and carrying out post-treatment on the deep denitrification treatment liquid, wherein the post-treatment comprises flocculation and fourth sludge-water separation in sequence, and the total phosphorus content in the treated water obtained by the post-treatment is less than 5 mg/L. According to the treatment method provided by the invention, before the anaerobic ammoxidation reaction, the kitchen waste biogas slurry is pretreated, solid suspended matters and oil substances in the kitchen waste biogas slurry can be effectively removed through flotation, and then organic matters and nitrogen in the kitchen waste biogas slurry are preliminarily removed through an anaerobic-aerobic secondary reaction; the obtained pretreatment liquid is subjected to anaerobic ammonia oxidation reaction, overload caused by high oil content, high solid suspended matter content, high organic matter content and high nitrogen content in the kitchen waste biogas slurry to the anaerobic ammonia oxidation reaction can be effectively avoided, the treatment stability of the anaerobic ammonia oxidation reaction is improved, most ammonia nitrogen, nitrate nitrogen and organic matters in the pretreatment liquid are removed through the anaerobic ammonia oxidation reaction of anaerobic ammonia oxidizing bacteria, the ammonia nitrogen content in the obtained anaerobic ammonia oxidation reaction clear liquid is less than 50mg/L, and the nitrate nitrogen content is less than 200 mg/L; then, carrying out aerobic-anaerobic-aerobic three-stage reaction on the anaerobic ammonia oxidation reaction clear liquid, further reducing the nitrogen content and the organic matter content in the anaerobic ammonia oxidation reaction clear liquid, and further improving the stability of the nitrogen content of the treated water; finally removing phosphorus in the deep denitrification treatment liquid through flocculation, and reducing the total phosphorus content in the treatment water obtained by post-treatment to be less than 5mg/L to reach the discharge standard. The kitchen waste biogas slurry treatment method provided by the invention carries out pretreatment, advanced treatment and post-treatment on the basis of anaerobic ammonia oxidation treatment, solves the problem that the anaerobic ammonia oxidation process is difficult to start and operate due to high suspended matter, COD concentration and grease concentration of the kitchen waste biogas slurry, reduces the using amount and power consumption of water treatment agents by adopting the anaerobic ammonia oxidation treatment, ensures the stability of the kitchen waste biogas slurry treatment effect, reduces the using amount of the water treatment agents by adopting the anaerobic ammonia oxidation treatment, can realize the stable treatment of the kitchen waste biogas slurry, ensures that the treated biogas slurry meets the emission standard and has low treatment cost.
The invention provides a treatment system used in the treatment method of kitchen waste biogas slurry, which comprises the following steps: a flotation device 15, said flotation device 15 being provided with a liquid discharge; the feeding hole of the first anaerobic tank 13 is communicated with the liquid discharging hole of the flotation equipment 15, and the first anaerobic tank 13 is also provided with a discharging hole; a first aerobic tank 14 with a feed inlet communicated with a discharge outlet of the first anaerobic tank 13, wherein the first aerobic tank 14 is also provided with a discharge outlet; a liquid inlet of the first sedimentation tank 110 is communicated with a liquid outlet of the first aerobic tank 14, and the first sedimentation tank 110 is also provided with a liquid outlet; the anaerobic ammonia oxidation reaction tank 23 is provided with a feed inlet communicated with the liquid discharge outlet of the first sedimentation tank 110, and the anaerobic ammonia oxidation reaction tank 23 is also provided with a discharge outlet; a liquid inlet of the second sedimentation tank 24 is communicated with a liquid outlet of the anaerobic ammonia oxidation reaction tank 23, and the second sedimentation tank 24 is also provided with a liquid outlet; a second aerobic tank 31 with a feed inlet communicated with a liquid discharge outlet of the second sedimentation tank 24, wherein the second aerobic tank 31 is also provided with a discharge outlet; a second anaerobic tank 33 with a feeding hole communicated with the discharging hole of the second aerobic tank 31, wherein the second anaerobic tank 33 is also provided with a discharging hole; a third aerobic tank 34 with a feed inlet communicated with the discharge outlet of the second anaerobic tank 33, wherein the third aerobic tank 34 is also provided with a discharge outlet; a liquid inlet of the third sedimentation tank 35 is communicated with a liquid outlet of the third aerobic tank 34, and the third sedimentation tank 35 is also provided with a liquid outlet; the feed inlet is communicated with the liquid discharge port of the third sedimentation tank 35, and the flocculation device is also provided with a discharge port; the liquid feed inlet with the fourth sedimentation tank 47 of flocculation device's discharge gate intercommunication, fourth sedimentation tank 47 still is provided with the liquid discharge gate. According to the treatment system provided by the invention, the flotation equipment 15, the first anaerobic tank 13, the first aerobic tank 14, the first sedimentation tank 110, the anaerobic ammonia oxidation reaction tank 23, the second sedimentation tank 24, the second aerobic tank 31, the second anaerobic tank 33, the third aerobic tank 34, the third sedimentation tank 35, the flocculation device and the fourth sedimentation tank 47 are sequentially communicated, so that pretreatment, advanced treatment and post-treatment can be carried out on the kitchen waste biogas slurry on the basis of anaerobic ammonia oxidation treatment, the stability of the kitchen waste biogas slurry treatment effect is ensured, the amount of water treatment agents is reduced by adopting anaerobic ammonia oxidation treatment, the stable treatment of the kitchen waste biogas slurry can be realized, and the treated biogas slurry meets the discharge standard and has low treatment cost.
Drawings
Fig. 1 is a schematic view of a kitchen waste biogas slurry treatment system provided by an embodiment of the invention;
wherein, 1-pretreatment system, 11-kitchen waste biogas slurry storage container, 12-kitchen waste biogas slurry delivery pump, 13-first anaerobic tank, 14-first aerobic tank, 15-flotation equipment, 16-first water treatment agent adding device, 17-second water treatment agent adding device, 18-first stirrer, 19-first aerator, 110-first sedimentation tank, 111-first sludge reflux pump, 112-first sludge pump, 113-first online dissolved oxygen tester, 114-first blower, 115-first gas regulating valve, 2-anaerobic ammonia oxidation system, 21-second gas regulating valve, 22-second online dissolved oxygen tester, 23-anaerobic ammonia oxidation reaction tank, 24-second sedimentation tank, 25-first online nitrate nitrogen tester, 26-a first online ammonia nitrogen measuring instrument, 27-an intermediate water temporary storage tank, 28-a gas flowmeter, 29-a second aerator, 210-a first water reflux pump, 211-a second air blower, 212-a second sludge reflux pump, a 3-deep nitrogen removal system, 31-a second aerobic tank, 32-a second online ammonia nitrogen measuring instrument, 33-a second anaerobic tank, 34-a third aerobic tank, 35-a third sedimentation tank, 36-a third aerator, 37-a second stirrer, 38-a second online nitrate nitrogen measuring instrument, 39-a carbon source adding device, 310-a second water reflux pump, 311-a third sludge reflux pump, 312-a second sludge discharge pump, 313-a third air blower, 314-a fourth aerator, 315-a third regulating valve and a 4-post-treatment system, 41-a flocculation tank, 42-a coagulation tank, 43-a third stirrer, 44-a fourth stirrer, 45-a third water treatment agent adding device, 46-a fourth water treatment agent adding device, 47-a fourth sedimentation tank and 48-a third sludge discharge pump.
Detailed Description
The invention provides a treatment method of kitchen waste biogas slurry, which comprises the following steps:
pretreating the kitchen waste biogas slurry to obtain a pretreatment solution, wherein the pretreatment comprises the steps of sequentially carrying out flotation, first anaerobic reaction, first aerobic reaction and first mud-water separation;
sequentially carrying out anaerobic ammoxidation reaction and second sludge-water separation on the pretreatment solution to obtain an anaerobic ammoxidation reaction clear solution, wherein the ammonia nitrogen content in the anaerobic ammoxidation reaction clear solution is less than 50mg/L, and the nitrate nitrogen content in the anaerobic ammoxidation reaction clear solution is less than 200 mg/L;
carrying out deep denitrification treatment on the anaerobic ammonia oxidation reaction clear solution to obtain deep denitrification treatment liquid, wherein the deep denitrification treatment comprises sequentially carrying out second aerobic reaction, second anaerobic reaction, third aerobic reaction and third sludge-water separation, the ammonia nitrogen content in the second aerobic reaction liquid obtained by the second aerobic reaction is less than 20mg/L, and the nitrate nitrogen content in the second anaerobic reaction liquid obtained by the second anaerobic reaction is less than 20 mg/L;
and carrying out post-treatment on the deep denitrification treatment liquid, wherein the post-treatment comprises flocculation and fourth sludge-water separation in sequence, and the total phosphorus content in the treated water obtained by the post-treatment is less than 5 mg/L.
In the present invention, the starting materials are all commercially available products well known to those skilled in the art, unless otherwise specified.
According to the invention, the kitchen waste biogas slurry is pretreated to obtain pretreatment liquid, and the pretreatment comprises the steps of sequentially carrying out flotation, first anaerobic reaction, first aerobic reaction and first mud-water separation.
In the invention, the Chemical Oxygen Demand (COD) of the kitchen waste biogas slurry is preferably less than 10000mg/L, the ammoniacal nitrogen content of the kitchen waste biogas slurry is preferably less than 2500mg/L, and the Total Nitrogen (TN) content of the kitchen waste biogas slurry is preferably less than 3000 mg/L.
In the invention, the kitchen waste biogas slurry is subjected to flotation to obtain flotation feed liquid.
In the present invention, the flotation is preferably gas flotation, and more preferably gas flotation with the addition of a flotation agent.
In the invention, the feeding flow rate of the kitchen waste biogas slurry subjected to the flotation is preferably 12m3/h。
In the present invention, the raw material for flotation preferably further comprises a first water treatment agent.
In the present invention, the first water treatment agent preferably includes polyaluminum chloride (PAC) and Polyacrylamide (PAM).
In the invention, the feeding flow rate of the kitchen waste biogas slurry subjected to the flotation is preferably 12m3When the first water treatment agent preferably comprises PAC and PAM, the PAC isThe dosage of the PAM is preferably 500mg/L, and the dosage of the PAM is preferably 5 mg/L.
According to the invention, suspended matters (SS), a part of phosphate and a part of COD in the kitchen waste biogas slurry are preferably removed through flotation, and meanwhile, oil-water separation is carried out on the kitchen waste biogas slurry, so that most of grease can be removed.
In the invention, flotation slag is also obtained by flotation, and the feeding flow rate of the kitchen waste biogas slurry during the flotation is preferably 12m3The discharge amount of the flotation slag is preferably 1m at the time of/h3/h。
In the invention, the dosage of the activated sludge of the first anaerobic reaction is preferably 3000-5000 mg/L, and more preferably 3500-4800 mg/L.
According to the invention, the first anaerobic reaction is carried out under the content condition of the activated sludge, so that the preliminary treatment of organic matters and total nitrogen in the kitchen waste biogas slurry can be realized, and the stable operation of the subsequent anaerobic ammonia oxidation reaction is facilitated.
In the present invention, the first anaerobic reaction is preferably carried out under stirring.
In the invention, the dosage of the activated sludge of the first aerobic reaction is preferably 3000-5000 mg/L, and more preferably 3500-4800 mg/L.
According to the invention, the first aerobic reaction is carried out under the content condition of the activated sludge, so that the preliminary treatment of organic matters in the kitchen waste biogas slurry can be realized, and the stable proceeding of the subsequent anaerobic ammonium oxidation reaction is facilitated.
In the present invention, the first aerobic reaction is carried out under aeration conditions.
In the invention, the first aerobic reaction is carried out to obtain a first aerobic reaction solution.
In the invention, the first sludge-water separation is carried out to obtain the pretreatment liquid.
In the invention, the ammonia nitrogen content of the pretreatment liquid is preferably 700-900 mg/L, the COD content of the pretreatment liquid is preferably 3000-4000 mg/L, the temperature of the pretreatment liquid is preferably 34-36 ℃, and the Dissolved Oxygen (DO) content of the pretreatment liquid is preferably less than 0.5 mg/L.
In the present invention, the first sludge-water separation preferably further obtains a first separated sludge, and the present invention preferably further comprises refluxing a part of the first separated sludge to perform the first anaerobic reaction.
In the present invention, the reflux flow rate of the first separated sludge is preferably the sum of the flow rate of the flotation solution and the reflux flow rate of the anammox reaction clear solution.
According to the invention, the backflow flow of the first separated sludge is preferably controlled within the range, so that the sludge can be effectively prevented from accumulating in the sedimentation tank and causing sludge leakage in the sedimentation tank.
The invention preferably further comprises discharging the residual first separated sludge, wherein the calculation formula of the sludge discharge amount of the residual first separated sludge is shown as formula 2:
the sludge discharge amount of the first separated sludge is (Q)Inflow water×(SS0-SSe)+0.4×QInflow water×(COD0-CODe))/CRow boardFormula 2;
in the above formula 2, QInflow waterThe flow rate of the first aerobic reaction solution, SS0The content of suspended substances in the first aerobic reaction solution is SSeThe content of suspended matter, COD, in the pretreatment solution0Is the chemical oxygen demand, COD, of the first aerobic reaction liquideChemical oxygen demand, C, of the pretreatment liquidRow boardIs the volume percentage of the dry sludge in the first separated sludge.
The invention preferably calculates the sludge discharge amount of the first separated sludge according to formula 2, can accurately calculate the sludge discharge amount, guides the normal operation of the first anaerobic reaction and the first aerobic reaction, ensures that the microorganisms of the first anaerobic reaction and the first aerobic reaction have the proper reaction concentration, and elutes the microorganisms which are unfavorable for the operation of the first anaerobic reaction and the first aerobic reaction out of the system.
After the pretreatment liquid is obtained, sequentially carrying out anaerobic ammonia oxidation reaction and second sludge-water separation on the pretreatment liquid to obtain an anaerobic ammonia oxidation reaction clear liquid, wherein the ammonia nitrogen content in the anaerobic ammonia oxidation reaction clear liquid is less than 50mg/L, and the nitrate nitrogen content in the anaerobic ammonia oxidation reaction clear liquid is less than 200 mg/L.
In the invention, when the anaerobic ammonia oxidation reaction is carried out, the dissolved oxygen content of the pretreatment liquid is preferably less than 0.5mg/L, more preferably less than 0.45mg/L, the ammonia nitrogen content of the pretreatment liquid is preferably 700-900 mg/L, more preferably 750-850 mg/L, and the temperature of the pretreatment liquid is preferably 30-37 ℃, more preferably 34-36 ℃.
In the present invention, the anammox reaction is preferably carried out under aeration conditions.
In the invention, the second sludge-water separation is carried out to obtain the anaerobic ammonium oxidation reaction clear liquid.
In the invention, the ammonia nitrogen content in the anaerobic ammonia oxidation reaction clear liquid is less than 50mg/L, preferably 10-50 mg/L; the content of nitrate nitrogen in the anaerobic ammonia oxidation reaction clear liquid is less than 200mg/L, and preferably less than 150 mg/L.
In the invention, the content of nitrate nitrogen in the anaerobic ammonia oxidation reaction clear liquid is preferably 70-150 mg/L.
In the present invention, the second sludge-water separation preferably further produces a second separated sludge, and the second separated sludge is preferably refluxed to perform the anammox reaction.
After obtaining the anaerobic ammonia oxidation reaction clear solution, carrying out deep denitrification treatment on the anaerobic ammonia oxidation reaction clear solution to obtain a deep denitrification treatment solution, wherein the deep denitrification treatment comprises sequentially carrying out a second aerobic reaction, a second anaerobic reaction, a third aerobic reaction and a third mud-water separation, the second aerobic reaction is carried out to obtain a second aerobic reaction solution, the ammonia nitrogen content in the second aerobic reaction solution is less than 20mg/L, the second anaerobic reaction is carried out to obtain a second anaerobic reaction solution, and the nitrate nitrogen content in the second anaerobic reaction solution is less than 20 mg/L.
In the present invention, the treatment method preferably further comprises refluxing a part of the anammox reaction supernatant to perform the first anaerobic reaction.
In the invention, the reflux flow of the anaerobic ammoxidation clear liquid is preferably 1-3 times, and preferably 1.5-2 times of the flow of the flotation feed liquid.
In the present invention, it is preferable that a part of the clear anammox reaction liquid is refluxed to perform the first anaerobic reaction, so that the concentration of the first anaerobic reaction influent contaminant can be effectively diluted, a part of nitrate nitrogen generated by the anaerobic ammoxidation reaction is refluxed to the first anaerobic reaction stage, and denitrification is performed using a carbon source of raw water, so that the organic matter and the part of nitrate nitrogen can be removed.
In the present invention, the second aerobic reaction is preferably carried out under aeration conditions.
In the invention, the second aerobic reaction is carried out to obtain a second aerobic reaction liquid, and the ammonia nitrogen content in the second aerobic reaction liquid is less than 20mg/L, preferably less than 5 mg/L.
In the present invention, the second anaerobic reaction is preferably performed under stirring conditions.
In the present invention, the raw material for the second anaerobic reaction preferably further comprises a carbon source, and the calculation formula of the addition amount of the carbon source is as shown in formula 1:
the carbon source addition amount is 4 XQInflow water×(TN0-TNe) Carbon source COD equivalent formula 1;
in the formula 1, QInflow waterIs the flow rate of the second aerobic reaction liquid, TN0Is the total nitrogen content, TN, in the second aerobic reaction liquideIs the total nitrogen content in the second anaerobic reaction liquid.
According to the invention, the carbon source adding amount is preferably accurately calculated by the formula 1, so that accurate adding of the carbon source can be effectively realized, and the phenomenon that the medicament is wasted due to excessive adding or the water outlet exceeds the standard due to insufficient adding is prevented.
In the invention, the second anaerobic reaction liquid is obtained through the second anaerobic reaction, and the content of nitrate nitrogen in the second anaerobic reaction liquid is less than 20 mg/L.
In the present invention, the third aerobic reaction is preferably carried out under aeration conditions.
In the present invention, the third aerobic reaction obtains a third aerobic reaction liquid.
In the present invention, the treatment method preferably further comprises refluxing a part of the third aerobic reaction solution to perform the second aerobic reaction.
In the present invention, the reflux flow rate of the third aerobic reaction solution is preferably 1 to 3 times, and more preferably 1.5 to 2.5 times, the flow rate of the clear anammox reaction solution in which the second aerobic reaction is performed.
In the present invention, the third sludge-water separation preferably further obtains a third separated sludge, and the present invention preferably further comprises returning a part of the third separated sludge to perform the second aerobic reaction.
In the present invention, the reflux flow rate of the second separated sludge is preferably the same as the flow rate of the clear anammox reaction solution in which the second aerobic reaction is carried out.
The invention preferably further comprises discharging the remaining third separated sludge, wherein the calculation formula of the sludge discharge amount of the remaining third separated sludge is shown as formula 3:
the sludge discharge amount of the third separated sludge is 1.6 XQInflow water(TN0-TNe)/CRow boardFormula 3;
in said formula 3, QInflow waterIs the flow rate of the remaining third aerobic reaction liquid, TN0Total nitrogen content, TN, in the remaining third aerobic reaction solutioneThe total nitrogen content, C, in the deep denitrification treatment liquidRow boardIs the volume percentage content of the dry sludge in the third separated sludge.
The sludge discharge amount of the third separated sludge is preferably calculated by the formula 3, the sludge discharge amount of the third separated sludge can be accurately determined, and excessive or insufficient sludge discharge is effectively prevented from influencing the treatment effect.
After the deep denitrification treatment liquid is obtained, the deep denitrification treatment liquid is subjected to post-treatment, the post-treatment comprises flocculation and fourth mud-water separation in sequence, and the total phosphorus content in the treatment water obtained by the post-treatment is less than 5 mg/L.
In the present invention, the flocculation preferably includes sequentially performing the first flocculation and the second flocculation.
In the present invention, the first flocculated feedstock preferably further comprises a second water treatment agent, which preferably comprises PAC and/or polyferric sulfate.
In the present invention, the second flocculated raw material preferably further includes a third water treatment agent, and the third water treatment agent preferably includes PAM.
In the invention, the feeding flow rate of the kitchen waste biogas slurry subjected to the flotation is preferably 12m3When the first flocculated raw material preferably comprises PAC, the dosage of the PAC is preferably 200 mg/L; when the raw material for the second flocculation preferably comprises PAM, the dosage of the PAM is preferably 5 mg/L.
In the present invention, the fourth sludge-water separation is performed to obtain treated water.
In the present invention, the total phosphorus content in the treated water is < 5mg/L, more preferably < 4.5mg/L
In the present invention, the COD content of the treated water is preferably < 500 mg/L; the content of ammoniacal nitrogen in the treated water is preferably less than 35 mg/L; the TN content in the treated water is preferably less than 45 mg/L.
In the present invention, the fourth sludge-water separation preferably further produces a fourth separated sludge, and the fourth separated sludge is discharged.
The invention provides a treatment system used in the treatment method of kitchen waste biogas slurry, which comprises the following steps:
a flotation device 15, said flotation device 15 being provided with a liquid discharge;
the feeding hole of the first anaerobic tank 13 is communicated with the liquid discharging hole of the flotation equipment 15, and the first anaerobic tank 13 is also provided with a discharging hole;
a first aerobic tank 14 with a feed inlet communicated with a discharge outlet of the first anaerobic tank 13, wherein the first aerobic tank 14 is also provided with a discharge outlet;
a liquid inlet of the first sedimentation tank 110 is communicated with a liquid outlet of the first aerobic tank 14, and the first sedimentation tank 110 is also provided with a liquid outlet;
the anaerobic ammonia oxidation reaction tank 23 is provided with a feed inlet communicated with the liquid discharge outlet of the first sedimentation tank 110, and the anaerobic ammonia oxidation reaction tank 23 is also provided with a discharge outlet;
a liquid inlet of the second sedimentation tank 24 is communicated with a liquid outlet of the anaerobic ammonia oxidation reaction tank 23, and the second sedimentation tank 24 is also provided with a liquid outlet;
a second aerobic tank 31 with a feed inlet communicated with a liquid discharge outlet of the second sedimentation tank 24, wherein the second aerobic tank 31 is also provided with a discharge outlet;
the feeding hole of the second anaerobic tank 33 is communicated with the discharging hole of the second aerobic tank, and the second anaerobic tank 33 is also provided with a discharging hole;
a third aerobic tank 34 with a feed inlet communicated with the discharge outlet of the second anaerobic tank 33, wherein the third aerobic tank 34 is also provided with a discharge outlet;
a liquid inlet of the third sedimentation tank 35 is communicated with a liquid outlet of the third aerobic tank 34, and the third sedimentation tank 35 is also provided with a liquid outlet;
the feed inlet is communicated with the liquid discharge port of the third sedimentation tank 35, and the flocculation device is also provided with a discharge port;
the liquid feed inlet with the fourth sedimentation tank 47 of flocculation device's discharge gate intercommunication, fourth sedimentation tank 47 still is provided with the liquid discharge gate.
The treatment system provided by the invention preferably further comprises a kitchen waste biogas slurry storage container 11, wherein the kitchen waste biogas slurry storage container 11 is used for storing the kitchen waste biogas slurry.
As a specific embodiment of the invention, the kitchen waste biogas slurry storage container 11 is provided with a discharge hole.
As a specific embodiment of the invention, the flotation device 15 is further provided with a liquid feeding hole, and the liquid feeding hole of the flotation device 15 is communicated with the discharging hole of the kitchen waste biogas slurry storage container 11.
As a specific embodiment of the invention, a kitchen waste biogas slurry delivery pump 12 is arranged at one end of a pipeline communicated with a discharge port of the kitchen waste biogas slurry storage container 11, which is close to the discharge port of the kitchen waste biogas slurry storage container 11.
The treatment system provided by the invention comprises a flotation device 15, said flotation device 15 being provided with a liquid discharge.
In the invention, the flotation equipment 15 is used for performing flotation on the kitchen waste biogas slurry.
As a specific embodiment of the present invention, the flotation equipment 15 is provided with a first water treatment agent adding device 16 and a second water treatment agent adding device 17.
As a specific embodiment of the invention, the flotation device 15 is provided with a slag discharge.
As a specific embodiment of the present invention, the flotation device 15 is an air-floating all-in-one machine.
The treatment system provided by the invention comprises a first anaerobic tank 13 with a feeding hole communicated with a liquid discharging hole of the flotation equipment 15, and the first anaerobic tank 13 is also provided with a discharging hole.
In the present invention, the first anaerobic tank 13 is used for performing a first anaerobic reaction treatment on the feed liquid entering the first anaerobic tank 13.
As an embodiment of the invention, a first stirrer 18 is arranged in the first anaerobic tank 13.
As an embodiment of the invention, the bottom surface of the first anaerobic tank 13 is provided with a sludge return inlet.
As a specific embodiment of the invention, the storefront of the first anaerobic tank 13 is provided with a feed liquid return inlet.
The treatment system provided by the invention comprises a first aerobic tank 14 with a feeding hole communicated with a discharging hole of the first anaerobic tank 13, and the first aerobic tank 14 is also provided with a discharging hole.
In the present invention, the first aerobic tank 14 is used for performing a first aerobic treatment on the feed liquid entering the first aerobic tank 14.
In an embodiment of the present invention, a first aerator 19 is disposed in the first aerobic tank 14.
As an embodiment of the present invention, the first aerator 19 is disposed on the bottom surface of the first aerobic reaction tank.
As an embodiment of the present invention, the first aerator 19 is in communication with a first blower 114.
In an embodiment of the present invention, a first air volume adjusting valve 115 is disposed at one end of the gas pipeline, which is in communication with the first aerator 19, of the first blower 114, and is close to one end of the first blower 114.
In an embodiment of the present invention, a first online dissolved oxygen meter 113 is disposed in the first aerobic reaction tank 14.
The treatment system provided by the invention comprises a first sedimentation tank 110 with a liquid feeding hole communicated with a discharging hole of the first aerobic tank 14, and the first sedimentation tank 110 is also provided with a liquid discharging hole.
In the present invention, the first sedimentation tank 110 is used for performing a first sludge-water separation.
As an embodiment of the present invention, the first sedimentation tank 110 is further provided with a sludge outlet.
As an embodiment of the present invention, the sludge outlet of the first settling tank 110 is disposed at the vertex of the conical bottom surface of the first settling tank 110.
As an embodiment of the present invention, the sludge outlet of the first sedimentation tank 110 is communicated with a first sludge pipeline.
As an embodiment of the invention, the first sludge conduit is provided with a first sludge return conduit and a first sludge discharge conduit.
As an embodiment of the present invention, the first sludge return pipe is communicated with a sludge return inlet on the bottom surface of the first anaerobic reaction tank 13.
As an embodiment of the present invention, a first sludge recirculation pump 111 is disposed at one end of the first sludge recirculation pipe close to the first sludge recirculation pipe.
As an embodiment of the present invention, a first sludge discharge pump 112 is disposed at one end of the first sludge discharge pipe close to the first sludge discharge pipe.
The treatment system provided by the invention comprises an anaerobic ammonia oxidation reaction tank 23 with a feeding hole communicated with a liquid discharging hole of the first sedimentation tank 110, wherein the anaerobic ammonia oxidation reaction tank 23 is also provided with a discharging hole.
In the present invention, the anammox reaction tank 23 is used for performing an anammox reaction on the feed liquid entering the anammox reaction tank 23.
In an embodiment of the present invention, a second aerator 29 is disposed in the anammox reaction tank 23.
In an embodiment of the present invention, the second aerator 29 is disposed on the bottom surface of the anammox reaction tank 23.
As an embodiment of the present invention, the second aerator 29 is a micro-porous aerator.
As an embodiment of the present invention, the second aerator 29 is in communication with a second blower 211.
In an embodiment of the present invention, a second air volume adjusting valve 21 is disposed at one end of the second blower 211 near a gas pipeline where the second blower 211 is communicated with the second aerator 29.
In an embodiment of the present invention, a gas flow meter 28 is disposed at one end of the gas pipeline, which is in communication with the second aerator 29, of the second blower 211, and is close to the second aerator 29.
In an embodiment of the present invention, a second online dissolved oxygen meter 22 is disposed in the anammox reaction tank 23.
In an embodiment of the present invention, a sludge return inlet is provided on the bottom surface of the anammox reaction tank 23.
The treatment system provided by the invention comprises a second sedimentation tank 24 with a liquid feeding hole communicated with a discharging hole of the anaerobic ammonia oxidation reaction tank 23, and the second sedimentation tank 24 is also provided with a liquid discharging hole.
In the present invention, the second sedimentation tank 24 is used for performing a second sludge-water separation.
As an embodiment of the present invention, the second sedimentation tank 24 is further provided with a sludge outlet.
As an embodiment of the present invention, the sludge outlet of the second settling tank 24 is disposed at the vertex of the conical bottom surface of the second settling tank 24.
As an embodiment of the present invention, the sludge outlet of the second sedimentation tank 24 is communicated with a second sludge return pipe.
In an embodiment of the present invention, the first sludge return line is communicated with a sludge return inlet on the bottom surface of the anammox reaction tank 23.
In an embodiment of the present invention, a first online nitrate nitrogen determinator 25 is disposed in the second sedimentation tank 24.
In an embodiment of the present invention, a first on-line ammoniacal nitrogen measuring instrument 26 is disposed in the second sedimentation tank 24.
The treatment system provided by the invention preferably further comprises an intermediate water temporary storage tank 27 with a feeding hole communicated with the liquid discharging hole of the second sedimentation tank 24, and the intermediate water temporary storage tank 27 is also provided with a discharging hole.
As an embodiment of the present invention, the bottom surface of the intermediate water temporary storage tank 27 is further provided with a feed liquid reflux outlet.
As an embodiment of the present invention, the feed liquid reflux outlet at the bottom of the intermediate water temporary storage tank 27 is communicated with the feed liquid at the bottom of the first anaerobic reaction tank 13.
As an embodiment of the present invention, a first water reflux pump 210 is disposed at one end of the pipeline, which is communicated with the feed liquid reflux outlet of the bottom surface of the intermediate water temporary storage tank 27 and is close to the feed liquid reflux outlet of the intermediate water temporary storage tank 27.
The treatment system provided by the invention comprises a second aerobic tank 31 with a feed inlet communicated with a liquid discharge outlet of the second sedimentation tank 24, and the second aerobic tank 31 is also provided with a discharge outlet.
As an embodiment of the present invention, the feed inlet of the second aerobic tank 31 is communicated with the discharge outlet of the intermediate temporary water storage tank 27.
In the present invention, the second aerobic tank 31 is used for performing a first aerobic reaction treatment on the feed liquid entering the second aerobic tank 31.
In an embodiment of the present invention, a third aerator 36 is disposed in the second aerobic tank 31.
As an embodiment of the present invention, the third aerator 36 is disposed on the bottom surface of the second aerobic tank 31.
As an embodiment of the present invention, the third aerator 36 is a raisable aerator.
As an embodiment of the present invention, the third aerator 36 is in communication with a third blower 313.
As an embodiment of the present invention, the gas outlet of the third blower 313 is communicated with one end of a gas main, the other end of the gas main is communicated with a first gas branch and a second gas branch, the first gas branch is communicated with the third aerator 36, and the gas main is provided with a third gas amount adjusting valve 315.
In an embodiment of the present invention, a second online ammoniacal nitrogen determinator 32 is disposed in the second aerobic tank 31.
As an embodiment of the invention, the bottom surface of the second aerobic tank 31 is provided with a sludge return inlet.
As an embodiment of the invention, the bottom surface of the second aerobic tank 31 is provided with a feed liquid reflux inlet.
The treatment system provided by the invention comprises a second anaerobic tank 33 with a feeding hole communicated with a discharging hole of the second aerobic tank 31, and the second anaerobic tank 33 is also provided with a discharging hole.
As a specific embodiment of the invention, the second anaerobic tank 33 is provided with a carbon source adding device 39.
In an embodiment of the present invention, a second stirrer 37 is disposed in the second anaerobic tank 33.
In an embodiment of the present invention, a second online nitrate nitrogen determinator 38 is disposed in the second anaerobic tank 33.
The treatment system provided by the invention comprises a third aerobic tank 34 with a feeding hole communicated with a discharging hole of the second anaerobic tank 33, and the third aerobic tank 34 is also provided with a discharging hole.
In the present invention, the third aerobic tank 34 is used for carrying out a third aerobic reaction treatment on the feed liquid entering the third aerobic tank 34.
In an embodiment of the present invention, a fourth aerator 314 is disposed in the third aerobic tank 34.
As an embodiment of the present invention, the fourth aerator 314 is disposed on the bottom surface of the third aerobic tank 34.
As an embodiment of the present invention, the fourth aerator 314 is a raisable aerator.
As an embodiment of the present invention, the fourth aerator 314 is in communication with the third blower 313.
As an embodiment of the present invention, the gas outlet of the third blower 313 is communicated with one end of a gas main, the other end of the gas main is communicated with a first gas branch and a second gas branch, the second gas branch is communicated with the fourth aerator 314, and the gas main is provided with a third gas amount adjusting valve 315.
As an embodiment of the invention, the bottom surface of the third aerobic tank 34 is provided with a feed liquid reflux outlet.
In an embodiment of the present invention, the feed liquid reflux outlet disposed on the bottom surface of the third aerobic tank 34 is communicated with the feed liquid reflux inlet disposed on the bottom surface of the second aerobic reaction tank 3.
In an embodiment of the present invention, a second water reflux pump 310 is disposed at one end of the pipeline, which is connected to the feed liquid reflux outlet disposed on the bottom surface of the third aerobic tank 34, and is close to the feed liquid reflux outlet disposed on the bottom surface of the third aerobic tank 34.
The treatment system provided by the invention comprises a third sedimentation tank 35 with a liquid inlet communicated with a discharge hole of the third aerobic tank 34, and the third sedimentation tank 35 is also provided with a liquid discharge hole.
In the present invention, the third sedimentation tank 35 is used for performing a third sludge-water separation.
As an embodiment of the present invention, the third sedimentation tank 35 is further provided with a sludge outlet.
As an embodiment of the present invention, the sludge outlet of the third settling tank 35 is disposed at the vertex of the conical bottom surface of the third settling tank 35.
As an embodiment of the present invention, the sludge outlet of the third sedimentation tank 35 is communicated with a second sludge pipeline.
As a specific example of the present invention, the second sludge line is provided with a third sludge return line and a second sludge discharge line.
As an embodiment of the present invention, the third sludge return pipe is communicated with the sludge return inlet on the bottom surface of the second aerobic reaction tank 31.
As an embodiment of the present invention, a third sludge recirculation pump 311 is disposed at one end of the third sludge recirculation pipe close to the second sludge recirculation pipe.
As an embodiment of the present invention, a second sludge pump 312 is disposed at one end of the second sludge discharging pipe near the second sludge pipe.
The treatment system provided by the invention comprises a flocculation device, wherein a feeding hole of the flocculation device is communicated with a liquid discharging hole of the third sedimentation tank 35, and the flocculation device is also provided with a discharging hole.
As a specific embodiment of the present invention, the flocculation device includes a flocculation tank 41 and a coagulation tank 42, the flocculation tank 41 is provided with a feed inlet and a discharge outlet, the coagulation tank is provided with a feed inlet and a discharge outlet, the discharge outlet of the flocculation tank 41 is communicated with the liquid discharge outlet of the third sedimentation tank 35, and the feed inlet of the coagulation tank is communicated with the discharge outlet of the flocculation tank 41.
As an embodiment of the present invention, a third stirrer 43 is disposed in the flocculation tank 41.
As a specific embodiment of the present invention, the flocculation tank 41 is provided with a third water treatment agent adding device 45.
As an embodiment of the present invention, the third water treatment agent adding device 45 is disposed above the flocculation tank 41.
In an embodiment of the present invention, a fourth stirrer 44 is disposed in the coagulation basin 42.
As an embodiment of the present invention, the coagulation tank 42 is provided with a fourth water treatment agent adding device 46.
As an embodiment of the present invention, the fourth water treatment agent adding device 46 is disposed above the coagulation tank 42.
The treatment system provided by the invention comprises a fourth sedimentation tank 47 with a liquid feeding hole communicated with a discharging hole of the flocculation device, and the fourth sedimentation tank 47 is also provided with a liquid discharging hole.
As an embodiment of the present invention, the feed inlet of the fourth sedimentation tank 47 is communicated with the discharge outlet of the coagulation tank 42.
As an embodiment of the present invention, the fourth sedimentation tank 47 is further provided with a sludge outlet.
As an embodiment of the present invention, the sludge outlet of the fourth settling tank 47 is disposed at the vertex of the conical bottom surface of the fourth settling tank 47.
As an embodiment of the present invention, the sludge outlet of the fourth sedimentation tank 47 is connected to a third sludge discharge pipe.
The technical solution of the present invention will be clearly and completely described below with reference to the embodiments of the present invention. It is to be understood that the described embodiments are merely exemplary of the invention, and not restrictive of the full scope of the invention. All other embodiments, which can be derived by a person skilled in the art from the embodiments given herein without making any creative effort, shall fall within the protection scope of the present invention.
Example 1
Treating certain kitchen waste biogas slurry according to the schematic view of the treatment system of the kitchen waste biogas slurry shown in figure 1, wherein the kitchen waste biogas slurry treated by a certain kitchen project is 150m3D, anaerobic fermentation is carried out on the kitchen waste, and products after fermentation are centrifugally removedThe water and the kitchen waste biogas slurry generated after centrifugal dehydration are 200m3And d, the COD content of the kitchen waste biogas slurry is less than 10000mg/L, the ammonia nitrogen content is less than 2500mg/L, the TN content is less than 3000mg/L, the effluent of treated water requires the COD content to be less than 500mg/L, the ammonia nitrogen content is less than 35mg/L, and the TN content is less than 45 mg/L.
The kitchen waste biogas slurry enters a kitchen waste biogas slurry storage container 11, after the kitchen waste biogas slurry stays for 2-3d, the kitchen waste biogas slurry enters a pretreatment system 1 through a kitchen waste biogas slurry conveying pump 12, and the amount of inlet water conveyed by the kitchen waste biogas slurry conveying pump 12 is 12m3And h, in the air floatation all-in-one machine 15, the PAC adding amount is 500mg/L, the PAM adding amount is 5mg/L, suspended matters, partial phosphate and partial COD in the wastewater are removed, meanwhile, oil-water separation is carried out on the kitchen waste biogas slurry, most of grease is removed, and the sludge discharge amount of the air floatation all-in-one machine 13 is 1m 3/h. The effluent of the air floatation all-in-one machine 15 enters a first anaerobic tank 13, wherein the reflux flow of the anaerobic ammonia oxidation reaction clear liquid refluxed by the intermediate water temporary storage tank is 20m3The sludge returns to the first anaerobic reaction tank 13 through the first water return pump 210, and the sludge return quantity of the first sedimentation tank 110 to the first anaerobic reaction tank 13 is 31m3The sludge discharge amount of the first settling tank 110 is 3m3The ammonia nitrogen content in effluent of the pretreatment feed liquid is 700-900 mg/L, the COD content is 3000-4000 mg/L, the temperature is 34-36 ℃, and the DO is less than 0.5 mg/L.
The pretreated material liquid enters an anaerobic ammonia oxidation reaction tank 23, most of ammoniacal nitrogen and total nitrogen in the pretreated material liquid are removed by anaerobic ammonia oxidation bacteria, effluent of the anaerobic ammonia oxidation reaction tank 23 automatically flows to a second sedimentation tank 24 for second mud-water separation, second sludge generated by the second sedimentation tank 24 returns to the anaerobic ammonia oxidation reaction tank 23 through a second sludge reflux pump 212, and the sludge reflux amount is 28m3And h, the ammonia nitrogen content of the anaerobic ammonia oxidation reaction clear liquid obtained from the effluent of the second sedimentation tank 24 is 10-50 mg/L, and the nitrate nitrogen content is 70-150 mg/L.
Part of the clear liquid of the anaerobic ammonia oxidation reaction enters a second aerobic reverse tank 31 of the deep denitrification system 3, the content of ammoniacal nitrogen in the effluent of the second aerobic reaction liquid obtained by the second aerobic tank is less than 5mg/L, and the content of nitrate nitrogen in the effluent of the second anaerobic reaction liquid obtained by the second anaerobic reaction tank 33 is less than20mg/L, the return amount of the sludge from the third sedimentation tank 35 to the second aerobic reaction tank 31 is 10m3H, the feed liquid amount of the third aerobic reaction tank 34 which flows back to the second aerobic reaction tank 31 is 16m3H is used as the reference value. And the deep denitrification treatment liquid obtained by mud-water separation in the third sedimentation tank enters the post-treatment system 4 and flows into a flocculation tank 41, PAC is added into the flocculation tank 41, the adding amount of PAC is 200mg/L, the effluent of the flocculation tank flows into a coagulation tank 42, PAM is added into the coagulation tank 42, the adding amount of PAM is 5mg/L, and the TP content in the effluent of the treated water obtained by post-treatment is below 5mg/L, so that the standard discharge is realized.
Comparative example 1
The process was substantially the same as in example 1, except that: only using the anaerobic ammonia oxidation system 2 in fig. 1 to treat the kitchen waste biogas slurry: the kitchen waste treated by a certain kitchen project is 150m3D, performing anaerobic fermentation on the kitchen waste, performing centrifugal dehydration on a product after fermentation, wherein the biogas slurry of the kitchen waste generated after centrifugal dehydration is 200m3And d, the COD content of the kitchen waste biogas slurry is less than 10000mg/L, the ammonia nitrogen content is less than 2500mg/L, and the TN content is less than 3000 mg/L.
The anammox reaction does not run normally because no pretreatment is performed.
Comparative example 2
The process was substantially the same as in example 1, except that: only the pretreatment system 1 and the anaerobic ammonia oxidation system 2 in the graph 1 are used for treating the kitchen waste biogas slurry to obtain treated water, the ammonia nitrogen content in the anaerobic ammonia oxidation reaction clear liquid of the treated water is 50mg/L, the TN content is 150mg/L, and the discharge standard is not met.
Comparative example 3
The process was substantially the same as in example 1, except that: only the pretreatment system 1, the anaerobic ammonia oxidation system 2 and the deep denitrification system 3 in the figure 1 are used for treating the kitchen waste biogas slurry to obtain treated water, wherein the COD content in the anaerobic ammonia oxidation reaction clear liquid of the treated water is 600-700 mg/L, the TP content is 10mg/L, and the discharge standard is not met.
Comparative example 4
The process was substantially the same as in example 1, except that: only the anaerobic ammonia oxidation system 2 and the deep denitrification system 3 in the figure 1 are used for treating the kitchen waste biogas slurry, a large amount of sludge is discharged by the anaerobic ammonia oxidation system, and anaerobic ammonia oxidizing bacteria are discharged from the system, so that the system cannot operate.
Comparative example 5
The process was substantially the same as in example 1, except that: the anaerobic ammonia oxidation system 2 and the post-treatment system 4 in fig. 1 are only used for treating the kitchen waste biogas slurry, and the anaerobic ammonia oxidation reaction cannot normally run because the pretreatment is not carried out.
The foregoing is only a preferred embodiment of the present invention, and it should be noted that, for those skilled in the art, various modifications and decorations can be made without departing from the principle of the present invention, and these modifications and decorations should also be regarded as the protection scope of the present invention.

Claims (10)

1. A treatment method of kitchen waste biogas slurry is characterized by comprising the following steps:
pretreating the kitchen waste biogas slurry to obtain a pretreatment solution, wherein the pretreatment comprises the steps of sequentially carrying out flotation, first anaerobic reaction, first aerobic reaction and first mud-water separation;
sequentially carrying out anaerobic ammoxidation reaction and second sludge-water separation on the pretreatment solution to obtain an anaerobic ammoxidation reaction clear solution, wherein the ammonia nitrogen content in the anaerobic ammoxidation reaction clear solution is less than 50mg/L, and the nitrate nitrogen content in the anaerobic ammoxidation reaction clear solution is less than 200 mg/L;
carrying out deep denitrification treatment on the anaerobic ammonia oxidation reaction clear solution to obtain deep denitrification treatment liquid, wherein the deep denitrification treatment comprises sequentially carrying out second aerobic reaction, second anaerobic reaction, third aerobic reaction and third sludge-water separation, the ammonia nitrogen content in the second aerobic reaction liquid obtained by the second aerobic reaction is less than 20mg/L, and the nitrate nitrogen content in the second anaerobic reaction liquid obtained by the second anaerobic reaction is less than 20 mg/L;
and carrying out post-treatment on the deep denitrification treatment liquid, wherein the post-treatment comprises flocculation and fourth sludge-water separation in sequence, and the total phosphorus content in the treated water obtained by the post-treatment is less than 5 mg/L.
2. The treatment method according to claim 1, wherein the amount of the activated sludge for the first anaerobic reaction and the first aerobic reaction is 3000 to 5000mg/L independently.
3. The method according to claim 1, wherein the anaerobic ammonia oxidation reaction is performed at a temperature of 30 to 37 ℃ in which the dissolved oxygen content of the pretreatment solution is less than 0.5mg/L, the ammonia nitrogen content of the pretreatment solution is 700 to 900mg/L, and the temperature of the pretreatment solution is set to 0 to 37 ℃.
4. The treatment method according to any one of claims 1 to 3, wherein the kitchen waste biogas slurry is subjected to flotation to obtain a flotation feed liquid;
the treatment method further comprises refluxing a part of the anaerobic ammonium oxidation reaction clear liquid to perform the first anaerobic reaction;
and the backflow flow of the anaerobic ammonia oxidation reaction clear liquid is 1-3 times of the flow of the flotation feed liquid.
5. The treatment method according to claim 4, wherein the first sludge-water separation further produces a first separated sludge, and further comprising refluxing a portion of the first separated sludge to perform the first anaerobic reaction; and the reflux flow of the first separated sludge is the sum of the flow of the flotation solution and the reflux flow of the anaerobic ammonia oxidation reaction clear solution.
6. The treatment method according to claim 1, wherein the raw material for the second anaerobic reaction further comprises a carbon source, and the formula for calculating the addition amount of the carbon source is shown as formula 1:
the carbon source addition amount is 4 XQInflow water×(TN0-TNe) Carbon source COD equivalent formula 1;
in the formula 1, QInflow waterIs the flow rate of the second aerobic reaction liquid, TN0Is the total content of the second aerobic reaction liquidNitrogen content, TNeIs the total nitrogen content in the second anaerobic reaction liquid.
7. The process according to claim 1, wherein the second sludge-water separation further produces a second separated sludge, and the second separated sludge is refluxed to perform the anammox reaction.
8. The treatment method according to claim 4, wherein the third aerobic reaction produces a third aerobic reaction liquid;
the processing method further comprises the following steps: refluxing a part of the third aerobic reaction liquid to perform the second aerobic reaction;
and the reflux flow rate of the third aerobic reaction liquid is 1-3 times of the flow rate of the anaerobic ammonia oxidation reaction clear liquid for carrying out the second aerobic reaction.
9. The treatment method according to claim 4, wherein the third sludge-water separation further results in a third separated sludge;
the treatment method further comprises refluxing a portion of the third separated sludge for the second aerobic reaction; the reflux flow rate of the second separated sludge is the same as the flow rate of the anaerobic ammonia oxidation reaction clear liquid for carrying out the second aerobic reaction.
10. The treatment system used in the treatment method of kitchen waste biogas slurry as recited in claim 1, comprising:
a flotation device (15), said flotation device (15) being provided with a liquid discharge;
a first anaerobic tank (13) with a feeding hole communicated with a liquid discharging hole of the flotation equipment (15), wherein the first anaerobic tank (13) is also provided with a discharging hole;
a first aerobic tank (14) with a feeding hole communicated with a discharging hole of the first anaerobic tank (13), wherein the first aerobic tank (14) is also provided with a discharging hole;
a liquid inlet of the first sedimentation tank (110) is communicated with a liquid outlet of the first aerobic tank (14), and the first sedimentation tank (110) is also provided with a liquid outlet;
the feeding hole of the anaerobic ammonia oxidation reaction tank (23) is communicated with the liquid discharging hole of the first sedimentation tank (110), and the anaerobic ammonia oxidation reaction tank (23) is also provided with a discharging hole;
a liquid feeding hole is communicated with a discharging hole of the anaerobic ammonia oxidation reaction tank (23), and the second sedimentation tank (24) is also provided with a liquid discharging hole;
a second aerobic tank (31) with a feed inlet communicated with a liquid discharge outlet of the second sedimentation tank (24), wherein the second aerobic tank (31) is also provided with a discharge outlet;
a second anaerobic tank (33) with a feeding hole communicated with a discharging hole of the second aerobic tank (31), wherein the second anaerobic tank (33) is also provided with a discharging hole;
a third aerobic tank (34) with a feed inlet communicated with a discharge outlet of the second anaerobic tank (33), wherein the third aerobic tank (34) is also provided with a discharge outlet;
a liquid inlet of the third sedimentation tank (35) is communicated with a discharge hole of the third aerobic tank (34), and the third sedimentation tank (35) is also provided with a liquid discharge hole;
the feed inlet is communicated with a liquid discharge port of the third sedimentation tank (35), and the flocculation device is also provided with a discharge port;
the liquid feeding hole is communicated with a discharge hole of the flocculation device, and the fourth sedimentation tank (47) is also provided with a liquid discharge hole.
CN202210192275.4A 2022-03-01 2022-03-01 Treatment method and treatment system for kitchen waste biogas slurry Pending CN114560595A (en)

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