CN116161820A - Kitchen waste anaerobic digestion liquid effluent treatment system and method - Google Patents
Kitchen waste anaerobic digestion liquid effluent treatment system and method Download PDFInfo
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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
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- C—CHEMISTRY; METALLURGY
- C02—TREATMENT OF WATER, WASTE WATER, SEWAGE, OR SLUDGE
- C02F—TREATMENT OF WATER, WASTE WATER, SEWAGE, OR SLUDGE
- C02F1/00—Treatment of water, waste water, or sewage
- C02F1/20—Treatment of water, waste water, or sewage by degassing, i.e. liberation of dissolved gases
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- C—CHEMISTRY; METALLURGY
- C02—TREATMENT OF WATER, WASTE WATER, SEWAGE, OR SLUDGE
- C02F—TREATMENT OF WATER, WASTE WATER, SEWAGE, OR SLUDGE
- C02F1/00—Treatment of water, waste water, or sewage
- C02F1/52—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
- C02F2103/00—Nature of the water, waste water, sewage or sludge to be treated
- C02F2103/06—Contaminated groundwater or leachate
-
- 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
- C02F2301/04—Flow arrangements
- C02F2301/046—Recirculation with an external loop
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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
- C02F3/00—Biological treatment of water, waste water, or sewage
- C02F3/30—Aerobic and anaerobic processes
-
- 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
- C02F3/302—Nitrification and denitrification treatment
- C02F3/307—Nitrification and denitrification treatment characterised by direct conversion of nitrite to molecular nitrogen, e.g. by using the Anammox process
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- Life Sciences & Earth Sciences (AREA)
- Hydrology & Water Resources (AREA)
- Engineering & Computer Science (AREA)
- Environmental & Geological Engineering (AREA)
- Water Supply & Treatment (AREA)
- Chemical & Material Sciences (AREA)
- Organic Chemistry (AREA)
- Separation Using Semi-Permeable Membranes (AREA)
Abstract
The invention provides a kitchen waste anaerobic digestion liquid effluent treatment system and a method, wherein the kitchen waste anaerobic digestion liquid effluent treatment system comprises the following components: the pretreatment system is used for removing most oily pollutants, suspended solid particles and COD (chemical oxygen demand) from the water discharged from the anaerobic digestion tank of the centrifuged kitchen waste through a pretreatment process; the high-efficiency denitrification system is used for realizing the denitrification of the effluent with large specific gravity through the PNA reactor by controlling the temperature and distributing water; the post-treatment system is sequentially connected with the anoxic tank, the multistage aerobic tank and the membrane bioreactor, and the final effluent is subjected to carbon removal and denitrification through denitrification and nitration reaction; and the sludge treatment system is used for treating sludge discharged from the pretreatment system and the high-efficiency denitrification system and residual sludge of the post-treatment system. The application realizes high-efficient and low-carbon sewage treatment effect through the system, and final water will circulate for inside water of system and factory self-water simultaneously, increases the resource retrieval and utilization, reduces operation and treatment cost.
Description
Technical Field
The invention relates to the field of sewage treatment, in particular to a kitchen waste anaerobic digestion liquid effluent treatment system and method.
Background
In recent years, along with the continuous improvement of economic development and living standard, a large amount of kitchen waste is gradually generated in daily life of the national, and at present, the kitchen waste treatment in China mainly takes landfill and incineration as main parts, and the kitchen waste recovery treatment in an anaerobic digestion technology is relatively low. The kitchen waste is solid waste rich in organic matters, high biomass energy is stored, and compared with the traditional landfill treatment or incineration treatment, the anaerobic digestion treatment of the kitchen waste can efficiently utilize the organic waste, generate renewable resources and develop carbon economy.
However, the application of anaerobic digestion of kitchen wastes also has technical problems, and one of the reasons for limiting the popularization of the anaerobic digestion is the problem of treatment of kitchen waste digestion liquid. Anaerobic digestion of kitchen wastes can produce extremely high concentration of ammonia nitrogen, volatile fatty acid and other pollutants in kitchen waste digestive juice besides biogas which can be used as renewable energy. Traditionally, biochemical a/O processes for treating these contaminants in kitchen digestate require large amounts of energy (e.g., excess aeration) and materials (e.g., make-up sugar and methanol), however, the treatment is often poorly suited. Although the physicochemical treatment processes such as ammonia stripping and the like have remarkable effect of treating high-concentration ammonia nitrogen, the high-energy consumption treatment process is contrary to the low-carbon concept of current sustainable development.
Therefore, how to treat the kitchen waste anaerobic digestion liquid efficiently and at low carbon is a problem to be solved at present.
Disclosure of Invention
In the present invention, some of the content incorporates a number of concepts in simplified form such as sewage treatment system flow diagrams and process flow simulation diagrams, which are described in detail in the detailed description section. The summary of the invention is not intended to define the key features and essential features of the claimed subject matter, nor is it intended to be used as an aid in determining the scope of the claimed subject matter.
Aiming at the problems existing in the existing kitchen waste digestive juice treatment, the invention provides a comprehensive treatment system and method for the digestive juice effluent after kitchen waste anaerobic digestion, which are used for removing various pollutants in sewage in stages through the combination of different reaction processes, comprehensively improving the efficiency of a treatment system, reducing the energy consumption of the treatment system and continuously promoting the efficient treatment and sustainable operation of sewage treatment.
In order to achieve the above object, in one aspect, the present invention provides a treatment system for kitchen waste anaerobic digestion liquid effluent. The kitchen waste anaerobic digestion liquid effluent treatment system comprises a pretreatment system, a high-efficiency denitrification system, a post-treatment system and a sludge treatment system.
Further, the pretreatment system comprises a water inlet adjusting cylinder, a dissolved air floatation system, a high-efficiency aeration tank and an associated inclined plate sedimentation cylinder, and is mainly used for separating out grease and suspended particulate matters in sewage, so as to promote removal of COD (chemical oxygen demand) containing the grease.
Furthermore, the dissolved air flotation system of the pretreatment system pumps flocculating agent and coagulant into different positions of a tubular mixing facility, adjusts pH simultaneously, comprehensively promotes the realization of flocculation and coagulation reaction, and implements mud-water separation by means of an air flotation device with saturated compressed air and a distributed horizontal solid-liquid separation device.
Furthermore, the high-efficiency aeration tank of the pretreatment system controls aeration quantity, DO control, a water distribution system and hydraulic retention time, and the actual numerical value of the set hydraulic retention time is required to be adjusted according to the site condition and is generally not more than 10 hours.
Furthermore, a water distribution system and an aeration device with self-cleaning and maintenance-free functions are arranged in the efficient aeration tank of the pretreatment system, and the aeration device is used for realizing uniform distribution of sewage, aeration control, DO control and water distribution control.
Furthermore, the inlet water in the pretreatment system is supernatant fluid of the kitchen waste anaerobic digestion liquid obtained by centrifuging the kitchen waste anaerobic digestion liquid, and if the inlet water of the pretreatment system is not subjected to solid-liquid separation, a front-end centrifugal separation device is required to be arranged according to actual conditions.
Furthermore, the high-efficiency denitrification system consists of a front-end regulating tank, a heat exchanger, a PNA reactor and a water outlet regulating tank and is used for removing most ammonia nitrogen (more than 80%).
Furthermore, the front end regulating tank of the high-efficiency denitrification system receives the effluent from the inclined plate sedimentation tank of the pretreatment system as dilution water, and also receives the circulating water of the PNA effluent regulating tank, so as to ensure the stability of ammonia nitrogen load at the water inlet end of the PNA reactor, thereby ensuring denitrification efficiency.
Further, a PNA water inlet regulating tank in the high-efficiency denitrification system is connected with the heat exchanger to provide temperature control for inlet water of the PNA reactor.
Furthermore, the hot water of the heat exchanger of the efficient denitrification system is from the hot circulating water of the kitchen waste digestion tank, so that the energy utilization efficiency is improved, the water inlet temperature of the hot circulating water is about 90 ℃, the water outlet temperature is about 70 ℃, the water inlet of the heat exchanger is controlled to be split in a system setting mode, and the aim of stably heating the water inlet of the heat exchanger to 33 ℃ is fulfilled.
Further, the post-treatment system comprises an anoxic tank, an aerobic tank A, an aerobic tank B and an MBR membrane bioreactor which are connected in series, and is mainly used for further removing residual ammonia nitrogen and COD.
Furthermore, the aerobic cylinders in the post-treatment system are all in a jet aeration mode and are used for supplying compact bubbles to the inlet water of the post-treatment system and ensuring DO concentration and water flow turbulence.
Furthermore, the aerobic cylinder in the post-treatment system can be provided with a diving diversion device for ensuring the turbulent flow state of water flow of the post-treatment system.
Further, the MBR membrane bioreactor in the post-treatment system adopts a PTFE ceramic membrane.
Further, the sludge treatment system receives sludge from the pretreatment system, the high efficiency denitrification system, and the post-treatment system.
Furthermore, supernatant liquid after the sludge storage cylinder of the sludge treatment system is precipitated can be actively conveyed to the front-end regulating tank through the liquid level control system, and concentrated sludge after the sludge storage cylinder is precipitated can be circulated to the kitchen waste digestion cylinder for treatment.
Further, the kitchen waste anaerobic digestion liquid effluent treatment system further comprises a comprehensive effluent regulating tank arranged at the tail end, wherein effluent of the comprehensive effluent regulating tank flows back to the anoxic tank or is discharged to a municipal sewage treatment plant or is discharged into a factory for recycling, and effluent of the comprehensive effluent regulating tank flows back to the anoxic tank for dilution operation.
Furthermore, the tail end of the kitchen waste anaerobic digestion liquid effluent treatment system can be provided with an advanced treatment system comprising a nanofiltration reverse osmosis system, and the advanced treatment system is used for producing high-standard reuse water. This part of the apparatus belongs to common general knowledge information and content of industry related persons, and does not relate to the important points of the present invention, so it is not repeated in this disclosure.
On the other hand, the invention provides a treatment method for kitchen waste anaerobic digestion liquid effluent, which comprises a pretreatment process of a pretreatment stage, a high-efficiency denitrification process of a high-efficiency denitrification stage and a post-treatment process of a post-treatment stage, wherein the treatment method for kitchen waste anaerobic digestion liquid effluent comprises the following steps:
step S201: a pretreatment stage, wherein part of grease, suspended solid particles and COD are removed and sludge is discharged from the supernatant of the kitchen waste anaerobic digestion liquid in the pretreatment process, and the effluent is conveyed to a high-efficiency aeration tank for high-efficiency BOD removal;
step S202: in the high-efficiency denitrification stage, the effluent water in the step S201 is heated (about 33 ℃) according to the high-efficiency denitrification process, and then nitrosation-anaerobic ammonia oxidation integrated reaction is carried out to realize high-efficiency ammonia nitrogen removal and sludge discharge, and the effluent water enters a post-treatment process;
step S203: a post-treatment stage, wherein the effluent of the high-efficiency denitrification stage in the step S202 sequentially passes through an anoxic-aerobic-membrane biological treatment unit according to the post-treatment process, so that denitrification, carbon removal, nitrification and high-efficiency filtration are realized, comprehensive removal of ammonia nitrogen, total nitrogen and suspended solids in the water and discharge of sludge are realized, and final effluent is obtained;
step S204: and a sludge treatment stage for conveying the sludge and solids separated, precipitated and precipitated by the pretreatment stage of the step S201, the high-efficiency denitrification stage of the step S202 and the post-treatment stage of the step S203 to a sludge storage cylinder.
Further, in step S204, the supernatant after precipitation is returned to the front-end adjusting tank of the pretreatment process, and the concentrated sludge after precipitation is sent to a kitchen waste digestion tank for co-digestion or concentrated clearing.
Further, the pretreatment process, the high-efficiency denitrification process and the biochemical reaction cylinder in the post-treatment process in the step S201, the step S202 and the step S203 are used for culturing activated sludge and/or biological membranes with different functions so as to realize different biochemical reactions.
Further, the water inlet in the pretreatment process in step S201 is a supernatant of the anaerobic kitchen waste digestion solution obtained by centrifuging the anaerobic kitchen waste digestion solution.
Further, in step S201, the dissolved air flotation system in the pretreatment system is used for performing mud-water separation by matching a flocculant with a coagulant through a jet device of saturated compressed air.
Further, the aeration rate, DO control, water distribution system and hydraulic retention time are controlled by the high-efficiency aeration tank in the pretreatment process in step S201.
Further, the nitrosation-anaerobic ammonia oxidation integrated reaction in step S202 is completed by the synergistic effect of the nitrosation reaction (1) performed by ammonia oxidizing bacteria and the anaerobic ammonia oxidation reaction (2) performed by anaerobic ammonia oxidizing bacteria, and the biochemical reaction formula is as follows.
Further, in step S202, the two microorganism populations involved in the nitrosation-anaerobic ammoxidation integrated reaction are specifically acclimatized and enriched by combining the PNA reactor in the efficient denitrification process with the biofilm based on MBBR biofilm carrier in a corresponding operation mode.
Further, in the post-treatment process in step S203, the biofilm of the biofilm carrier in the aerobic tank and the biofilm in the MBR membrane bioreactor realize synchronous nitrification and denitrification based on DO regulation.
Further, in the post-treatment process in step S203, an additional carbon source such as glucose and methanol needs to be added to perform heterotrophic denitrification to promote removal of nitrate nitrogen (including nitrite nitrogen), and continuous aerobic a and aerobic B stages in the post-treatment process respectively decompose residual carbon and nitrify residual ammonia nitrogen in the effluent of the anoxic tank.
Further, in the post-treatment process in step S203, the MBR membrane bioreactor obviously increases the sludge concentration under the condition of ensuring that the concentration of suspended particulate matters in the effluent is low, and under the condition of ensuring the DO concentration, the MBR membrane bioreactor can promote the realization of synchronous nitrification and denitrification, thereby not only effectively increasing the treatment load, but also enhancing the resistance to the fluctuation of hydraulic water quality.
Further, the final effluent in the post-treatment process in step S203 is conveyed to a comprehensive effluent adjusting tank in the post-treatment process, the effluent of the comprehensive effluent adjusting tank flows back to the anoxic tank or is discharged to a municipal sewage treatment plant or is discharged into a factory for reuse, and the effluent of the comprehensive effluent adjusting tank flows back to the anoxic tank for dilution operation.
Further, the sludge storage tank in the sludge treatment process in step S204 separates the final effluent in the post-treatment process in step S203 into supernatant and concentrated sludge after precipitation, the supernatant flows back to the front-end adjusting tank of the front-end treatment process, and the concentrated sludge can be sent to the kitchen waste digestion tank for digestion treatment, so that the treatment load on solid waste is further reduced, and the wastewater treatment tank is favorable for realizing zero waste discharge and resource circulation.
Compared with the prior art, the invention has the following beneficial effects:
the supernatant of the kitchen waste digestion tank has high concentration of BOD and grease, and extremely high concentration of ammonia nitrogen. The process can remove grease, BOD and part of suspended particles in the pretreatment stage respectively; in the high-efficiency denitrification stage, partial ammonia nitrogen is oxidized into nitrite nitrogen by utilizing functional nitrite bacteria, and simultaneously nitrite nitrogen and residual ammonia nitrogen are successfully converted into nitrogen by utilizing anammox bacteria, and a small amount of nitrate nitrogen and residual ammonia nitrogen generated in the anammox process can be thoroughly removed by utilizing an A/O treatment process (namely an anoxic-aerobic treatment unit) and an MBR membrane bioreactor in the post-treatment stage.
The process provided by the invention can separate BOD and grease associated with sewage in the early stage, and reduce the interference on nitrosation-anaerobic ammoxidation reaction. For sewage such as kitchen waste digestive juice, the treatment is often focused on ammonia nitrogen removal. The nitrosation-anaerobic ammonia oxidation integrated reaction adopted by the invention can utilize the functional microorganism to remove the ammonia nitrogen with large specific gravity, namely the specific gravity of the total amount of the removed ammonia nitrogen, under the conditions of low aeration, low energy consumption and low carbon emission. In contrast, the traditional treatment mode, such as a materialized ammonia stripping process, can realize the high-efficiency removal of ammonia nitrogen, but is often accompanied by extremely high direct energy consumption, and a large amount of chemical agents are needed to assist in driving the process, so that the post-treatment process of the collected ammonia nitrogen further increases the complexity of the process. Meanwhile, in the traditional biochemical treatment mode such as an A/O treatment process, ammonia nitrogen can be converted into nitrogen in a denitrification stage in a harmless mode, but a large amount of carbon sources are required to be supplemented in an anoxic stage, and meanwhile, a higher aeration rate and a higher reflux ratio are maintained in an aerobic stage. Compared with the prior art, the invention has the same general requirements of the current environmental engineering industry on low energy consumption, low resource requirement and low carbon emission.
Compared with heterotrophic bacteria for realizing the traditional denitrification function, the ammonia oxidizing bacteria and the anaerobic ammonia oxidizing bacteria are chemolithotrophic bacteria, so that high-efficiency denitrification is realized, and the energy consumption and the addition of medicaments such as carbon sources are greatly reduced. Meanwhile, the relative growth rate of autotrophic bacteria is low, so that the excess sludge generated by the nitrosation-anaerobic ammonia oxidation integrated reaction is relatively less, and the reflux of the sludge is reduced and the scale of the subsequent sludge treatment process is reduced through the design of the reactor. Furthermore, the two functional microorganism populations can be specifically domesticated and enriched by distributing activated sludge in the tank to MBBR biological fillers and corresponding operation modes, so that the functional bacteria can stay in the reaction tank for a long time, and the method has great significance for long-term stable operation of a factory.
Drawings
FIG. 1 is a schematic flow diagram of an embodiment of a system for treating effluent of kitchen waste anaerobic digestion liquid;
FIG. 2 is a process flow diagram of a second embodiment of a method for treating effluent of kitchen waste anaerobic digestion liquid;
fig. 3 is a schematic flow chart of a second embodiment of a method for treating effluent of anaerobic digestion liquid of kitchen waste.
The realization, functional characteristics and advantages of the present application will be further described with reference to the embodiments, referring to the attached drawings.
Detailed Description
In the following description, numerous specific details are set forth in order to provide a more thorough understanding of the present invention. It will be apparent, however, to one skilled in the art that the invention may be practiced without one or more of these details. In other instances, well-known features have not been described in detail in order to avoid obscuring the invention.
In order to provide a further thorough understanding of the present invention, detailed steps will be presented in the following description to illustrate the landfill leachate treatment system and treatment method of the present invention. It will be apparent that the invention is not limited to the specific details familiar to those skilled in the art. The preferred embodiments of the present invention are described in detail below, however, it should be understood that the present invention can be embodied in various forms and should not be construed as limited to the embodiments set forth herein. The terms "comprises," "comprising," and/or "including," when used in this specification, specify the presence of stated features, integers, steps, operations, elements, and/or components, but do not preclude the presence or addition of one or more other features, integers, steps, operations, elements, components, and/or groups thereof.
Example one
The invention provides a treatment system for kitchen waste anaerobic digestion liquid effluent, which is shown in fig. 1 and comprises a pretreatment system, a high-efficiency denitrification system, a post-treatment system and a sludge treatment system which are sequentially arranged. The pretreatment system comprises a front-end regulating tank, a dissolved air flotation system, a high-efficiency aeration tank and an inclined plate sedimentation tank which are sequentially arranged; the high-efficiency denitrification system comprises a PNA water inlet regulating tank, a heat exchanger, a PNA cylinder (namely a PNA reactor) and a PNA water outlet regulating tank which are sequentially arranged; the post-treatment system comprises an anoxic tank, an aerobic tank A, an aerobic tank B and a membrane bioreactor (which can be an MBR membrane bioreactor) which are sequentially arranged; the sludge treatment system is connected with the sludge discharge pipelines of the three systems and is provided with a sludge storage cylinder for collecting and storing all the surplus sludge.
The invention provides a treatment system for kitchen waste anaerobic digestion liquid effluent, wherein water inflow of the treatment system is supernatant liquid of the effluent of the kitchen waste anaerobic digestion liquid after centrifugal treatment, and a front-end regulating tank integrates the water quality and the water quantity of sewage. Wherein, the supernatant of the sludge storage cylinder can flow back to the front-end regulating tank for treatment. The sewage integrated by the front-end adjusting tank enters the dissolved air floatation system.
The dissolved air flotation system (Dissolved Air Flotation) comprises a tubular mixing facility, a compressed air aeration device and a high-efficiency reaction tank which are arranged at the front end. The tubular mixing facility mixes flocculating agent and coagulant at different positions, combines pH adjustment, comprehensively promotes realization of flocculation and coagulation reaction, and finally separates solids suspended on the liquid level of the high-efficiency reaction tank by means of an air floatation device rich in saturated compressed air and a circulating mechanical separation device. The anaerobic digestion liquid of kitchen waste contains volatile fatty acid VFA or other oily substances, and the volatile fatty acid VFA or other oily substances are removed along with suspended solid particles in sewage in a dissolved air flotation system. The effluent of the dissolved air flotation system enters the high-efficiency aeration tank, the high-efficiency aeration tank passes through a specific water distribution system, the impact of different hydraulic loads on the system can be coped with, and the active sludge can realize the removal of most of BOD under aeration without the removal of ammonia nitrogen by combining with the design of hydraulic retention time. The effluent of the high-efficiency aeration tank enters an inclined plate sedimentation tank for sedimentation. The sludge separated by chemical precipitation in the dissolved air flotation system, the surplus sludge in the high-efficiency aeration tank and the precipitated and concentrated sludge in the inclined plate sedimentation tank enter a sludge storage cylinder for further treatment.
The effluent from the inclined plate sedimentation tank enters a PNA water inlet regulating tank of the high-efficiency denitrification system. Because the sewage is rich in ammonia nitrogen with extremely high concentration, in order to ensure the follow-up reaction, the effluent of the comprehensive effluent regulating tank can partially return to the PNA effluent regulating tank according to the inflow amount of water, so that the concentration of the ammonia nitrogen in the inflow water is diluted to be half of that in the original PNA effluent regulating tank. By means of a temperature control system, the incoming water will be warmed up in the heat exchanger and kept at a water temperature of about 33 c throughout the year. Previous studies have shown that one key condition to ensure nitrosation-anaerobic ammoxidation is to ensure a stable supply of nitrous nitrogen. At this water temperature, the activity of the ammonia oxidizing bacteria (ammonia oxidizing bacteria) is greater than the activity of the nitrite oxidizing bacteria (Nitrite oxidizing bacteria), thereby ensuring the progress of ammonia oxidation and indirectly inhibiting the progress of nitrite oxidation. Meanwhile, the reaction rate of the anaerobic ammonia oxidation bacteria also increases due to the rise of the water temperature. Therefore, the heat exchanger provides an important temperature guarantee for nitrosation-anaerobic ammoxidation. The hot water in the heat exchanger comes from a temperature control circulating water system of the kitchen waste anaerobic digestion system, and no extra energy consumption exists. With strict DO and aeration control, most (80% or more) of the ammonia nitrogen in the wastewater in the PNA tank will be removed by the nitrosation-anammox reaction and the effluent from the PNA tank will enter the PNA effluent conditioning tank. If the effluent does not meet the removal effect of the original design, the effluent of the PNA effluent regulating tank can partially flow back to the PNA effluent regulating tank for recycling treatment. The excess sludge from the PNA cylinders will enter the sludge storage cylinders for further treatment, but due to the relatively low growth rate of ammonia oxidizing bacteria and anaerobic ammonia oxidizing bacteria, the PNA cylinders have little opportunity to perform frequent and significant excess sludge discharge.
The outlet water of the PNA outlet water regulating tank enters an anoxic tank of the aftertreatment system. In the anoxic tank operation, nitrate nitrogen (including nitrite nitrogen) in the sewage is removed by denitrification reaction of microorganisms by supplementing carbon sources (such as glucose, methanol, etc.). The effluent of the anoxic cylinder sequentially enters an aerobic cylinder A and an aerobic cylinder B, and the aerobic cylinder A and the aerobic cylinder B adopt jet aeration, so that BOD removal and complete oxidation of ammonia nitrogen are effectively ensured. Wherein, the water outlet part of the aerobic cylinder B can flow back to the anoxic cylinder to supplement nitrate nitrogen (comprising nitrite nitrogen). The effluent of the aerobic cylinder B enters a membrane bioreactor, and the membrane bioreactor can effectively ensure higher sludge concentration and excellent sewage outlet effect. The higher sludge concentration of the membrane bioreactor can provide greater resistance to water impact by the activated sludge system. The sludge part of the membrane bioreactor can flow back to the anoxic tank, and the residual sludge enters the sludge storage tank for further treatment.
Supernatant fluid precipitated by a sludge storage cylinder of the sludge treatment system is conveyed to the front-end regulating tank, and concentrated sludge precipitated by the sludge storage cylinder is circulated to the kitchen waste digestion cylinder for treatment.
The effluent of the membrane bioreactor flows into a comprehensive effluent regulating tank, and the effluent of the comprehensive effluent regulating tank flows back to an anoxic tank for dilution operation, or the effluent is used for factory reuse water, or is discharged to a municipal sewage treatment plant.
According to the embodiment of the application, the pretreatment system is used for effectively separating the VFA, the grease, the BOD and most of suspended solid particles in raw water, so that the interference effect of the pretreatment system on the high-efficiency denitrification unit is avoided, and the stability of the subsequent denitrification efficiency is maintained. Under the conditions of strict DO, aeration, temperature control and the like of the system, the sewage realizes the removal of large-proportion ammonia nitrogen in the high-efficiency denitrification system under the conditions of low energy consumption and low carbon emission through fewer operation procedures. Finally, the residual ammonia nitrogen is completely removed in a post-treatment system. Through the deep integration of the sewage treatment system, the treatment system for the kitchen waste anaerobic digestion liquid effluent saves a great amount of energy consumption on the basis of completing the high-efficiency denitrification treatment, effectively reduces the carbon emission, and provides a typical example for the implementation of the synergy of pollution reduction and carbon reduction.
Example two
The invention provides a treatment method of kitchen waste anaerobic digestion liquid effluent, which is shown in figure 2. The treatment method comprises a pretreatment process of a pretreatment stage, a high-efficiency denitrification process of a high-efficiency denitrification stage and a post-treatment process of a post-treatment stage, wherein the main steps of the treatment method for the kitchen waste anaerobic digestion liquid effluent are shown in figure 3:
step S201: a pretreatment stage, wherein part of grease, suspended solid particles and COD are removed and sludge is discharged from the supernatant of the kitchen waste anaerobic digestion liquid in the pretreatment process, and the effluent is conveyed to a high-efficiency aeration tank for high-efficiency BOD removal;
step S202: a high-efficiency denitrification stage, wherein the effluent in the step S201 is heated (about 33 ℃) according to the high-efficiency denitrification process, and then nitrosation-anaerobic ammonia oxidation integrated reaction is carried out to realize high-efficiency ammonia nitrogen removal and sludge discharge, and the effluent enters a post-treatment stage;
step S203: a post-treatment stage, namely sequentially passing the effluent through an anoxic-aerobic-membrane biological treatment unit according to the post-treatment process to realize denitrification, decarbonization, nitrification and high-efficiency filtration, and comprehensively remove ammonia nitrogen, total nitrogen and suspended solids in the water and discharge sludge to obtain final effluent;
step S204: and a sludge treatment stage, wherein the sludge and solids separated, precipitated and separated in the pretreatment stage of the step S201, the high-efficiency denitrification stage of the step S202 and the post-treatment stage of the step S203 are conveyed to a sludge storage cylinder, and supernatant liquid after the sludge storage cylinder is further precipitated is returned to a front-end regulating tank, so that concentrated sludge is concentrated and cleared.
The method for treating the effluent of the kitchen waste anaerobic digestion liquid is applicable to supernatant liquid after the kitchen waste anaerobic digestion liquid is separated, and in actual operation, the kitchen waste anaerobic digestion liquid can be subjected to rapid sludge settlement in a mechanical centrifugation mode, and the supernatant liquid after centrifugation is input into a pretreatment process for treatment; or settling the kitchen waste anaerobic digestion liquid through a settling tank, and taking effluent containing relatively less suspended solid particles as inlet water entering the pretreatment process. The kitchen waste anaerobic digestion process is simultaneously suitable for treating sewage with the same water quality as the water inflow, such as sewage containing grease, BOD and ammonia nitrogen with extremely high concentration, such as effluent of an anaerobic digestion system of kitchen waste or food processing industry waste.
Next, step S201 is executed, and in the pretreatment stage, the effluent of the kitchen waste anaerobic digestion liquid is sequentially subjected to partial removal of grease, suspended solid particles and COD and rapid solid-liquid separation in the pretreatment process, and the effluent of the kitchen waste anaerobic digestion liquid is conveyed to a high-efficiency aeration tank to be subjected to high-efficiency removal of BOD.
Illustratively, in a tubular coagulator, the pH of the wastewater is adjusted to neutral by first replenishing NaOH or other alkaline agent; adding 0.1% polyaluminium chloride PAC as a coagulant at the subsequent site of the tubular coagulation device, and rapidly separating out grease and soluble organic matters; and then adding a cationic polymeric flocculant at a subsequent site to coagulate the precipitated solid into macromolecular solid blocks, so that the subsequent air flotation separation is facilitated. If the influent water contains a large amount of refractory organic matters such as humic acid and the like, in order to avoid the influence on the subsequent process and effluent water quality, ferric chloride and neutral polyaluminium chloride are added as a coagulant to perform precipitation reaction under the acidic condition in actual operation.
Illustratively, to ensure effective and rapid removal of BOD in a high efficiency aeration tank, the COD and BOD concentration of the influent wastewater generally does not exceed 3000mg/L and 1000mg/L, and the suspended solid particle concentration does not exceed 1500mg/L. In order to ensure the water inlet concentration, the removal rate of the comprehensive suspended particles passing through the dissolved air flotation device is generally not less than 73%.
Next, executing step S202, and in a high-efficiency denitrification stage, heating (about 33 ℃) the effluent of the pretreatment process according to the high-efficiency denitrification process, and performing nitrosation-anaerobic ammonia oxidation integrated reaction to realize high-efficiency ammonia nitrogen removal and sludge discharge; the nitrosation-anaerobic ammonia oxidation integrated reaction is completed by the synergistic effect of an ammonia oxidation reaction (1) carried out by ammonia oxidizing bacteria and an anaerobic ammonia oxidation reaction (2) carried out by anaerobic ammonia oxidizing bacteria, and the related biochemical reaction formula is as follows.
The effluent from the step S201 is diluted, ammonia nitrogen in the effluent of the kitchen waste anaerobic digestion liquid can reach 2000-2800 mgN/L, and previous researches show that excessive ammonia nitrogen with high concentration can generate more free ammonia, thereby generating inhibition effect on ammonia oxidizing bacteria and generating negative effect on the whole reaction. Therefore, the final effluent is recycled to the PNA water inlet regulating tank, and the ammonia nitrogen concentration of the sewage is diluted (such as 100% dilution), so that the anaerobic ammonia oxidation reaction is facilitated.
By way of example, the ammonia oxidizing bacteria and anaerobic ammonia oxidizing bacteria can be inoculated and cultured by granular sludge in the existing mature process, the starting time of a newly built sewage treatment plant is generally not less than 3 months, and the existing project operation shows that the ammonia nitrogen removal efficiency can reach 80% or more.
Illustratively, the ammonia oxidizing bacteria and anaerobic ammonia oxidizing bacteria described above may also be enriched and cultured by means of activated sludge dosing with MBBR biofilm. Anaerobic ammonia oxidizing bacteria have a lower relative growth rate than ammonia oxidizing bacteria, and are therefore more suitable for enrichment and growth in the protective layer of MBBR biofilm. Ammonia oxidizing bacteria in the IFAS-MBBR process after long-term acclimation and operation will be more prone to be enriched in activated sludge, while anaerobic ammonia oxidizing bacteria will be more prone to be enriched on MBBR packing.
Next, executing step S203, and in a post-treatment stage, passing the effluent of the efficient denitrification process through an anoxic-aerobic-membrane biological treatment unit according to the post-treatment process in sequence, so as to realize denitrification, carbon removal, nitrification and efficient filtration, realize comprehensive removal of ammonia nitrogen, total nitrogen and suspended solids in the water, and discharge of sludge, and obtain final effluent;
illustratively, during the operation of the anoxic tank in the post-treatment process, by supplementing carbon sources (such as glucose, methanol and the like), nitrate nitrogen (including nitrite nitrogen) in the effluent of the efficient denitrification process is removed through denitrification reaction of microorganisms, and the arrangement of the aerobic tank A and the aerobic tank B effectively ensures the removal of BOD and the complete oxidation of ammonia nitrogen in the effluent of the anoxic tank. The effluent of the aerobic tank B enters an MBR (Membrane bioreactor), and the MBR effectively ensures higher sludge concentration and excellent sewage outlet effect. Higher sludge concentrations in the MBR membrane bioreactor can provide greater resistance to water impact by the activated sludge system. Sludge in the MBR membrane bioreactor can flow back to the anoxic tank, and the residual sludge enters the sludge storage tank for further treatment.
Illustratively, the denitrifying and nitrifying bacteria described above may also be enriched and cultured by means of activated sludge dosing with MBBR biofilm. Compared with the pure activated sludge process, the added MBBR biological filler can effectively increase the effective sludge concentration, is more particularly suitable for enrichment of nitrifying bacteria with relatively slow growth rate, and is beneficial to shortening the starting time.
Illustratively, the basic indexes of the effluent after the denitrification and the nitrification reactions and the MBR membrane bioreactor ensure that the concentration of COD and BOD is not more than 200mg/L and 20mg/L, the concentration of total nitrogen and ammonia nitrogen effluent is not more than 90mgN/L and 25mgN/L, and the concentration of total suspended solid particles is not more than 100mg/L, thereby realizing efficient and stable effluent.
Next, step S204 is performed, and the sludge treatment stage, in which the sludge and solids separated, precipitated and separated in the pretreatment stage of step S201, the efficient denitrification stage of step S202, and the post-treatment stage of step S203 are transferred to a sludge storage tank, and the supernatant after further precipitation in the sludge storage tank is returned to the front-end conditioning tank, and the concentrated sludge is collected and disposed.
In the pretreatment stage of step S201, sludge is generated in the front-end adjusting tank, the dissolved air floatation system and the inclined plate sedimentation tank in the pretreatment process, the PNA reactor in the high-efficiency denitrification stage generates sludge and solids after ammonia nitrogen removal reaction, the generated sludge is discharged into the sludge storage cylinder, part of sludge in the MBR membrane bioreactor flows back to the anoxic cylinder, and the residual sludge enters the sludge storage cylinder for further treatment.
The present invention has been illustrated by the above-described embodiments, but it should be understood that the above-described embodiments are for purposes of illustration and description only and are not intended to limit the invention to the embodiments described. In addition, it will be understood by those skilled in the art that the present invention is not limited to the embodiments described above, and that many variations and modifications are possible in light of the teachings of the invention, which variations and modifications are within the scope of the invention as claimed. The scope of the invention is defined by the appended claims and equivalents thereof.
The foregoing embodiment numbers of the present application are merely for describing, and do not represent advantages or disadvantages of the embodiments.
The foregoing description is only of the preferred embodiments of the present application, and is not intended to limit the scope of the claims, and all equivalent structures or equivalent processes using the descriptions and drawings of the present application, or direct or indirect application in other related technical fields are included in the scope of the claims of the present application.
Claims (10)
1. The kitchen waste anaerobic digestion liquid effluent treatment system is characterized by at least comprising a pretreatment system, a high-efficiency denitrification system, a post-treatment system and a sludge treatment system.
2. The kitchen waste anaerobic digestion liquid effluent treatment system according to claim 1, wherein the dissolved air flotation system in the pretreatment system is used for carrying out mud-water separation by matching a flocculating agent and a coagulant through a jet device of saturated compressed air; the high-efficiency aeration tank in the pretreatment system is used for controlling aeration quantity, DO control, a water distribution system and hydraulic retention time.
3. The kitchen waste anaerobic digestion liquid effluent treatment system according to claim 1, wherein the efficient denitrification system at least comprises a PNA water inlet regulating tank, a heat exchanger and a PNA reactor, wherein the PNA water inlet regulating tank is connected with the heat exchanger to provide temperature control for water inlet of the PNA reactor, and hot water of the heat exchanger is sourced from hot circulating water of the kitchen waste anaerobic digestion tank so as to achieve comprehensive cooperative utilization of a heat source; the PNA water inlet regulating tank receives the effluent of the front-end treatment system and the circulating water of the PNA water outlet regulating tank and is used for regulating the ammonia nitrogen concentration.
4. The kitchen waste anaerobic digestion liquid effluent treatment system according to claim 1, wherein the aerobic tank in the post-treatment system adopts jet aeration for supplying dense gas bubbles and maintaining DO concentration and turbulence state inside the water tank.
5. The kitchen waste anaerobic digestion liquid effluent treatment system according to claim 1, further comprising a comprehensive effluent regulating tank arranged at the tail end, wherein the comprehensive effluent regulating tank effluent flows back to an anoxic tank in the post-treatment system for dilution operation or other water in a factory or discharged to a municipal sewage treatment plant.
6. The method for treating the kitchen waste anaerobic digestion liquid effluent is characterized by comprising the following steps of:
step 1, in a pretreatment process, the supernatant fluid of kitchen waste anaerobic digestion liquid is subjected to partial removal of grease, suspended solid particles and COD and discharge of sludge in sequence, and effluent enters a high-efficiency denitrification process;
step 2, removing large-specific-gravity ammonia nitrogen and total nitrogen and discharging sludge from the effluent in a high-efficiency denitrification process, wherein the effluent enters a post-treatment process;
step 3, removing residual ammonia nitrogen, total nitrogen, BOD and suspended solid particles and discharging sludge from the effluent in a post-treatment process to obtain final effluent;
step 4, conveying the sludge discharged from the previous step to a sludge storage cylinder in a sludge treatment process;
and step 5, returning supernatant fluid precipitated by the sludge storage cylinder to a front-end regulating tank, and collecting and clearing concentrated sludge precipitated by the sludge storage cylinder.
7. The method for treating wastewater from a kitchen waste anaerobic digestion solution according to claim 6, wherein the wastewater from the pretreatment process is a supernatant of the kitchen waste anaerobic digestion solution obtained by centrifuging the kitchen waste anaerobic digestion solution.
8. The method for treating kitchen waste anaerobic digestion solution effluent according to claim 6, wherein the PNA reactor in the efficient denitrification process cultures activated sludge and biofilm based on MBBR biofilm, thereby facilitating enrichment of different kinds of microorganisms to achieve synergistic biochemical reactions of nitrosation and anaerobic ammoxidation.
9. The method for treating kitchen waste anaerobic digestion liquid effluent according to claim 6, wherein an anoxic tank and an aerobic tank in the post-treatment process culture activated sludge, simultaneously culture biological membranes based on MBBR biological fillers, and the high-efficiency denitrification process effluent passes through the anoxic tank, the aerobic tank and an MBR membrane bioreactor to realize synchronous nitrification and denitrification reaction based on DO regulation.
10. The method for treating kitchen waste anaerobic digestion liquid effluent according to claim 6, wherein the pretreatment process, the efficient denitrification process and the biochemical reaction cylinder in the post-treatment process cultivate active sludge and/or biological films with different functions to realize different biochemical reactions, and the biological films based on MBBR biological fillers cultivated in the biochemical reaction cylinder are beneficial to enrichment of microorganism populations with slower growth rate in the biochemical cylinder and strengthening of functionality.
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