CN112028243A - Quick starting method of biological membrane system - Google Patents
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- C02F3/00—Biological treatment of water, waste water, or sewage
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- C02F3/34—Biological treatment of water, waste water, or sewage characterised by the microorganisms used
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Abstract
The application relates to the field of biological denitrification treatment of water bodies such as municipal sewage, river overflow sewage and the like, in particular to a quick starting method of a biological membrane system, which comprises the following steps: step one, preparing a culture environment: filling the anoxic tank and the aerobic tank with filler, and then filling the anoxic tank and the aerobic tank with sewage to be treated; step two, adding a microbial inoculum: adding a denitrifying bacterium agent into the anoxic tank, and adding a nitrifying bacterium agent into the aerobic tank; dissolving, diffusing and stuffy aeration of the microbial inoculum; step four, expanding and culturing the microbial inoculum: step five, stably treating sewage: and continuously feeding water and refluxing to remove nitrogen-containing pollutants in the sewage after the amplification culture of the microbial inoculum is completed. The technical scheme of the application has the advantages of short film forming time, no residual sludge discharge, low operation cost, good pollutant removing effect, stable effluent quality, strong impact load resistance and the like.
Description
Technical Field
The application relates to the field of biological denitrification treatment of water bodies such as municipal sewage and river overflow sewage, in particular to a quick starting method of a biological membrane system.
Background
Municipal sewage and river overflow sewage are relatively stable in water quality, but turbid, deep, stink, slightly alkaline, high in nitrogen content and generally free of toxic substances. Municipal sewage is mainly water discharged from living facilities such as kitchens, toilets, bathrooms and laundries of residences, public facilities and factories, river overflow sewage is usually composed of mixed liquid of municipal pipe network sewage and rainwater, and the composition of pollutants is basically the same as that of municipal sewage but is slightly lower than that of the municipal sewage.
The activated sludge process is a common process for treating sewage, and has the advantages of large treatment capacity, strong treatment capacity, high treatment efficiency, good water storage quality and the like. However, the activated sludge system has the disadvantages of difficulty in obtaining higher biomass of denitrifying microorganisms and low nitrification efficiency, so that the autotrophic microorganism denitrifying system has weak impact resistance, incomplete nitrification, large occupied area, high capital investment and high operation maintenance and management difficulty. Based on the defects of sewage treatment by an activated sludge process, the biofilm process is gradually applied to sewage treatment, has stable operation, less residual sludge, simple management and strong removal capability on ammonia nitrogen and refractory pollutants, and can adapt to larger water quality range change.
In order to solve the problems commonly existing in the common biofilm culturing method, such as the defects of long time for denitrification microorganism biofilm culturing, poor adhesion, complex operation, low biomass, low impact load resistance and the like, the Chinese patent with the patent application number of 201710051574.5 discloses a rapid biofilm culturing method for a high-efficiency denitrification microorganism bacterium agent, and the technical key points of the method are as follows: high-concentration microorganisms enter the aerobic nitrification reactor from the top through an external circulation pipeline to form a solid-liquid flow from top to bottom in a biological filler area; meanwhile, bubbles formed by micropore aeration form gaseous flow from bottom to top in the biological filler area, the three are fully mixed in the biological filler area to form a fluidized state, and denitrification microorganisms are attached to or grow on the surface of the biological filler to gradually form a microorganism aggregate in the fluidized state so as to achieve the purpose of quick start. The scheme also needs to use simulated sewage to provide nutrients for the growth of microorganisms, and in addition, the scheme can achieve stability after the film formation is finished and the actual wastewater runs for 7-14 days. The patent mentions that the ammonia nitrogen concentration of the sewage is 50-100mg/L, the sewage with high ammonia nitrogen concentration is generally industrial wastewater, while the ammonia nitrogen concentration of general municipal sewage and river overflow sewage is generally lower than 50mg/L, so the scheme is not suitable for treating the sewage with low ammonia nitrogen concentration.
Aiming at the treatment of wastewater with low ammonia nitrogen concentration, the Chinese patent with the patent application number of 201610761797.6 discloses a rapid start method for a river channel repairing biofilm system in a step-by-step biofilm formation mode. However, the above process is complicated and troublesome to operate, and the SBR reactor needs to be transferred to a river channel simulation biofilm reactor provided with an aerator for acclimatization after membrane pre-suspension.
The activated sludge adopted in the related technologies is subjected to biofilm formation, the activated sludge contains a lot of microorganisms which can not degrade pollutants, the sludge concentration is 6000mg/L, the microorganisms can propagate in a large amount in sewage, the sludge concentration in reaction equipment is higher and higher, and the growth of beneficial microorganisms is influenced if the microorganisms are not discharged in time, so that the sludge is required to be discharged regularly, the treatment cost of the residual sludge is 700 yuan/ton at present, and the burden is brought to the production and operation of enterprises. And the related technologies can only treat ammonia nitrogen in the sewage, and have no treatment effect on total nitrogen in the sewage.
In view of the above-mentioned related art, the inventors have recognized a need to provide a fast start-up method for a biofilm system that overcomes the deficiencies of the related art.
Disclosure of Invention
Aiming at the defects in the prior art, the invention aims to provide a quick starting method of a biological membrane system, which has the advantages of low operation cost and no residual sludge discharge and can reduce the total nitrogen content in sewage.
In order to realize the purpose, the invention provides the following technical scheme that the quick starting method of the biological membrane system comprises the following starting steps:
step one, preparing a culture environment: filling the anoxic tank and the aerobic tank with filler, and then filling the anoxic tank and the aerobic tank with sewage to be treated;
step two, adding a microbial inoculum: adding a denitrifying bacterium agent into the anoxic tank, and adding a nitrifying bacterium agent into the aerobic tank;
step three, preliminary dissolution and diffusion of the microbial inoculum: starting a stirring device in the anoxic tank to perform anaerobic culture on the added denitrifying bacteria agent, and starting an aeration device in the aerobic tank to perform smoldering aeration on the added nitrifying bacteria agent;
step four, expanding and culturing the microbial inoculum: after the anaerobic culture and the aeration are finished, adding sewage into the anoxic tank, enabling the sewage to flow out after sequentially passing through the anoxic tank and the aerobic tank, adding the sewage into the anoxic tank, and simultaneously opening a backflow channel arranged between the aerobic tank and the anoxic tank to enable part of the sewage to flow back into the anoxic tank from the aerobic tank;
step five, stably treating sewage: continuously feeding water and refluxing to remove nitrogen-containing pollutants in the sewage after the amplification culture of the microbial inoculum is completed; wherein the sewage is municipal sewage or river overflow sewage;
wherein the denitrifying bacteria agent is a compound of pseudomonas stutzeri, micrococcus luteus, achromobacter denitrificans, a first biological enzyme and nutrient salt; the nitrifying agent is a compound of nitrosomonas, nitrobacteria, a second biological enzyme and nutrient salt.
By adopting the technical scheme, because the anoxic-aerobic circular treatment process is adopted, the total nitrogen content in the sewage can be reduced by the technical scheme, wherein the denitrifying bacteria agent added into the anoxic tank in the step two can reduce the nitrate into nitrogen by using sewage organic matters, and the nitrifying bacteria agent added into the aerobic tank oxidizes ammonia nitrogen into nitrate by using dissolved oxygen. In the anoxic tank, denitrifying bacteria can be attached to the filler in the dissolving and diffusing process, in the aerobic tank, aeration can be performed to enable nitrifying bacteria agents to be attached to the filler, the sewage added in the step one can only be used as nutrients required by the added bacteria agents to maintain life, after the dissolving, diffusing and aeration are completed, the nitrifying bacteria agents and the denitrifying bacteria agents are in a starvation state because nitrogen-containing organic matters added in the step one are digested, after the sewage is added again, the biomass in the anoxic tank and the aerobic tank can be rapidly increased, and after the biomass is stable, the sewage treatment system can begin to continuously treat the sewage. According to the method, the nitrifying bacteria and the denitrifying bacteria are adopted for biofilm formation, other useless microorganisms are not added into the reaction equipment, and the nitrifying bacteria and the denitrifying bacteria are mainly attached to the filler, so that the concentration of sludge in the reaction equipment is not high and is lower than 1000mg/L, the self-metabolism of the nitrifying bacteria and the denitrifying bacteria only occurs in the reactor, the amount of sludge generated in the process is small, the sludge can directly flow out of the reaction equipment along with effluent, and special discharge is not needed. The composite nitrifying bacteria agent and the composite denitrifying bacteria agent are selected, the pseudomonas stutzeri, the micrococcus luteus and the colorless denitrifying bacteria can form a stable ecological circle, alkaline protease generated by the pseudomonas stutzeri in the metabolic process has viscosity, the micrococcus luteus with small volume can be reduced to be dispersed in water, the micrococcus luteus with small volume surrounds the colorless denitrifying bacteria, nutrients which cannot be utilized by the colorless denitrifying bacteria are fully utilized, the composite bacteria agent can be better attached to fillers finally, the nutrients of all strains are guaranteed to be sufficient, the denitrifying process of sewage is completed cooperatively, and in the period that the ecological circle is not formed, the first biological enzyme and nutrient salt mainly can accelerate the formation of the ecological circle by the pseudomonas stutzeri, the micrococcus luteus and the colorless denitrifying bacteria. The nitrifying bacteria can attach to the nitrosomonas to form an ecological circle, the second biological enzyme and the nutrient salt can accelerate the process of attaching the nitrifying bacteria to the nitrosomonas, and the nitrifying bacteria and the nitrosomonas are compounded, so that the ammonia nitrogen in the sewage can be efficiently reduced. The complex of this application nitrobacter and denitrifying bacteria agent chooses for use the sewage treatment who reaches effectually, especially to municipal sewage and river course overflow sewage, the treatment effect is better than correlation technique, and the start-up time is shorter, and shock resistance is strong.
Further, the denitrifying bacteria agent is a compound of pseudomonas stutzeri BNCC-221999, micrococcus luteus BNCC-139548, achromobacter denitrificans BNCC-138371, a first biological enzyme and nutrient salt according to the mass ratio of 1:1:3:2: 1; the nitrifying bacteria agent is a compound of nitrosomonas CGMCC-11865, nitrobacteria CCTCC-M2019420, a second biological enzyme and nutrient salt according to the mass ratio of 3:2:1: 1.
By adopting the technical scheme, the starting effect achieved by the selection and proportion selection of the strains is shorter.
Further, the first biological enzyme is obtained by blending nitrate reductase, nitrite reductase, nitric oxide reductase and nitrous oxide reductase according to the mass ratio of 2:2:1: 1; the second biological enzyme is a nitrifying enzyme.
By adopting the technical scheme, the nitrate reductase, the nitrite reductase and the nitric oxide reductase can synergistically reduce nitrate and nitrite into nitrogen, and the denitrifying bacteria play a role in supplementing in the process of forming an ecological ring.
Further, the filler is one of carbon fiber, ecological grass and nylon fiber.
By adopting the technical scheme, the fillers of the types are all fillers capable of well loading the nitrifying bacteria agent and the denitrifying bacteria agent.
Further, when the filler is carbon fiber, the density of the carbon fiber is 200-400g/m3(ii) a When the filler is ecological grass, the density of the ecological grass is 150-300g/m3(ii) a When the filler is nylon fiber, the density of the nylon fiber is 400-500g/m3。
By adopting the technical scheme, higher ammonia nitrogen removal rate and total nitrogen removal rate can be achieved, and the ammonia nitrogen removal rate and the total nitrogen removal rate in the sewage can respectively reach 70-80% and 50-60%.
Furthermore, in the third step, the dissolving diffusion and the aeration time are both 1-2 days, and the time of the expanding culture of the microbial inoculum is 6-7 days.
By adopting the technical scheme, the dissolving, diffusing and stuffy aeration time of 1-2 days is long enough to make the nitrifying bacteria agent and the denitrifying bacteria agent attached to the filler, and the nutrient substances in the sewage added in the step one are completely consumed, and at the moment, the microorganisms in the anoxic pond and the aerobic pond are in a hungry state, so that preparation is made for expanded culture. Once the microorganisms in the starvation state obtain energy, the microorganisms are rapidly propagated, and the solid culture time is short.
Furthermore, in the fourth step and the fifth step, the concentration of the dissolved oxygen in the anoxic pond is required to be lower than 0.5mg/L, and the concentration of the dissolved oxygen in the aerobic pond is 1.5-2.5 mg/L.
By adopting the technical scheme, the denitrification reaction can be carried out only when the dissolved oxygen concentration required in the anoxic tank is below 0.5mg/L, and the reduction amount of the nitrate in the anoxic tank with the dissolved oxygen concentration higher than 0.5mg/L into nitrogen is reduced, so that the total nitrogen concentration of the effluent is increased. When the dissolved oxygen concentration in the aerobic tank is within the range of 1.5-2.5mg/L, the biological activity of the nitrifying bacteria agent is highest, the ammonia nitrogen in the sewage can be converted into nitrate most efficiently, when the dissolved oxygen is higher than 2.5mg/L, the required aeration amount is increased, the operation cost can be increased, and when the dissolved oxygen is lower than 1.5mg/L, the activity of the nitrifying bacteria can be influenced, so that the efficiency of converting the ammonia nitrogen into the nitrate is reduced, and the total nitrogen concentration of effluent is increased finally.
Further, in the fourth step and the fifth step, the mass ratio of the reflux quantity to the water inflow is (1.5-3): 1, the mass ratio of the water inflow to the water outflow is 1: 1.
By adopting the technical scheme, the proportion of the return flow of the nitrifying liquid to the water inflow in the sewage treatment process is fixed and is generally 1.5-3, because the growth speed of the nitrifying bacteria in the aerobic tank is different from that of the denitrifying bacteria in the anoxic tank, and the growth speed of the nitrifying bacteria is about twice as slow as that of the denitrifying bacteria. If the ratio of the return flow of the nitrifying liquid to the water inflow is too low, the nitrate cannot be completely converted into nitrogen, and the total nitrogen concentration of effluent is too high; if the ratio of the return flow of the nitrifying liquid to the water inflow is too high, the dissolved oxygen carried in the nitrifying liquid in the aerobic tank can influence the content of the dissolved oxygen in the anoxic tank. The water inflow and the water outflow should be equal, if the water inflow is higher than the water outflow for a long time, more and more sewage in the aerobic pool and the anoxic pool will be caused to overflow, and if the water inflow is lower than the water outflow for a long time, less and less sewage in the aerobic pool and the anoxic pool will be caused to fail to complete the sewage treatment.
Furthermore, the mass ratio of the denitrifying bacteria agent to the nitrifying bacteria agent is 1 (2-3).
By adopting the technical scheme, the growth speed of the denitrifying bacteria agent is one time faster than that of the nitrifying bacteria agent, and in order to keep the nitric acid capacity of ammonia nitrogen consistent with the denitrification capacity, the adding proportion of denitrifying bacteria and nitrifying bacteria is 2-3 times, so that the total nitrogen can be removed relatively high. If the adding ratio of denitrifying bacteria to nitrifying bacteria is lower than 2, the nitrifying efficiency is reduced, the removal rate of ammonia nitrogen is reduced, and the total nitrogen of effluent is increased. If the adding proportion of the denitrifying bacteria to the nitrifying bacteria is more than 3, because the attachment amount of the filler to the microorganisms is limited, when the proportion is 2-3, the attachment of the denitrifying bacteria and the nitrifying bacteria is basically saturated, and redundant nitrifying bacteria flow out of the aerobic tank along with effluent, so when the proportion is more than 3, the total nitrogen removal capacity is not obviously improved, but the investment cost of the nitrifying bacteria is increased.
Furthermore, the volume ratio of the anoxic tank to the aerobic tank is 1 (2-3).
By adopting the technical scheme, the growth speed of denitrifying bacteria is two times faster than that of nitrifying bacteria, and in order to keep the nitric acid capacity and the denitrification capacity of ammonia nitrogen consistent, the volume ratio of the anoxic tank to the aerobic tank is 1: (2-3). If the proportion is lower than 2, the nitrification capacity of the aerobic tank is lower, so that the concentration of ammonia nitrogen effluent is increased, and meanwhile, the concentration of nitrate in the return sewage is reduced, so that the amount of converted nitrogen is also reduced, the total nitrogen concentration of effluent is finally increased, and the total nitrogen removal capacity of the process is reduced. If the ratio is more than 3, the investment cost is increased, but the total nitrogen removal capacity is not significantly improved as compared with the ratio of 2.
In conclusion, the invention has the following beneficial effects:
firstly, the starting time of the technical scheme is short, compared with some technical schemes in the prior art, the starting time of the technical scheme is short, the biofilm formation can be completed in 7 days, and the sewage can be effectively treated;
secondly, the technical scheme is simple to operate, and only in-situ film hanging is carried out in the anoxic tank and the aerobic tank, and operations such as transferring fillers and the like are not needed as in the patent with the patent application number of 201610761797.6;
second, this application technical scheme does not have surplus sludge discharge, and the running cost is low, what this application biofilm formation in-process adopted is the raw water, and need use the simulation sewage among the technical scheme that patent application number is 201710051574.5, and the simulation sewage is formed by chemical agent configuration, needs purchase cost and medicament dosing equipment cost etc.. In addition, because the method has no excess sludge discharge, the purchase cost, the operation electricity cost, the operation maintenance cost and the like of the sludge discharge pump can be saved, and the disposal cost of the discharged sludge is saved;
thirdly, the effluent quality of the technical scheme is stable, the impact load resistance is strong, and when the concentration of ammonia nitrogen and total nitrogen in the sewage fluctuates greatly, the influence of the concentration change of the ammonia nitrogen and the total nitrogen in the inlet water on the effluent is small because the adaptability of a biological membrane formed by nitrobacteria and denitrifying bacteria is strong;
fourthly, the technical scheme of the application not only can reduce the content of ammonia nitrogen in the sewage, but also can reduce the content of total nitrogen in the sewage, the ammonia nitrogen is oxidized into nitrate under the action of nitrifying bacteria in the aerobic pool, the nitrate is reduced into nitrogen under the action of denitrifying bacteria in the anoxic pool, and the two are combined to achieve the purpose of removing the total nitrogen;
fifthly, the method can better treat municipal sewage and river overflow sewage, and the ammonia nitrogen removal rate and the total nitrogen removal rate can reach 70-80% and 50-60% respectively.
Drawings
FIG. 1 is a schematic diagram of an anoxic-aerobic process treatment tank as used herein.
Description of reference numerals: 1. an anoxic tank; 2. an aerobic tank; 3. a water inlet; 4. a water outlet; 5. a delivery channel; 6. a return channel; 7. a reflux pump.
Detailed Description
The present invention will be described in further detail with reference to the following drawings and examples.
Referring to fig. 1, it is first to be described that the anoxic-aerobic process treatment tank used in the method for quickly starting a biofilm system according to the embodiments of the present invention includes an anoxic tank 1 and an aerobic tank 2, the anoxic tank 1 is connected to a water inlet 3, a water inlet device (not shown) is disposed at the position of the water inlet 3, the anoxic tank is connected to a water outlet 3, a conveying channel 5 and a return channel 6 are disposed between the anoxic tank 1 and the aerobic tank 3, and a return pump 7 is disposed at the position of the return channel. The process can be better realized by using the sewage treatment tank, the water inlet device is started, the sewage can flow into the anoxic tank 1, the sewage in the anoxic tank 1 flows into the aerobic tank 2 through the conveying channel 5, under the action of the reflux pump 7, part of the sewage in the aerobic tank flows into the anoxic tank 1 through the reflux channel 6, and the other part of the sewage is discharged from the water outlet 4.
Example 1
A method for the rapid start-up of a biofilm system, comprising the process steps of:
step one, preparing a culture environment: filling the anoxic tank and the aerobic tank with filler, and then filling the anoxic tank and the aerobic tank with sewage to be treated; the fillers suspended in the anoxic tank and the aerobic tank are carbon fiber fillers, and the densities of the fillers are 300g/m2In this embodiment, the effective volume of the anoxic tank is 50L, and the effective volume of the aerobic tank is 100L.
Step two, adding a microbial inoculum: adding 25g of denitrifying bacteria agent into the anoxic tank, and adding 50g of nitrifying bacteria agent into the aerobic tank; the denitrifying bacteria agent is a compound of pseudomonas stutzeri BNCC-221999, micrococcus luteus BNCC-139548, denitrifying Achromobacter BNCC-138371, a first biological enzyme and nutrient salt according to the mass ratio of 1:1:3:2: 1; the nitrifying agent is a compound of nitrosomonas CGMCC-11865, nitrobacteria CCTCC-M2019420, a second biological enzyme and nutrient salt according to the mass ratio of 3:2:1: 1. The first biological enzyme is prepared by blending nitrate reductase, nitrite reductase, nitric oxide reductase and nitrous oxide reductase according to the mass ratio of 2:2:1: 1; the second biological enzyme is a nitrifying enzyme.
Step three, dissolving, diffusing and aerating the microbial inoculum: after the denitrifying bacteria agent is added into the anoxic tank, the denitrifying bacteria agent is naturally dissolved and diffused in the anoxic tank, after the nitrifying bacteria agent is added into the aerobic tank, an aeration device in the aerobic tank is started to carry out stuffy aeration on the added nitrifying bacteria agent, and the dissolving, the diffusing and the stuffy aeration are carried out simultaneously for one day.
Step four, expanding and culturing the microbial inoculum: after dissolution, diffusion and stuffy aeration are finished, adding sewage into the anoxic tank, enabling the sewage to flow out after sequentially passing through the anoxic tank and the aerobic tank, adding the sewage into the anoxic tank, and simultaneously opening a backflow channel arranged between the aerobic tank and the anoxic tank to enable part of the sewage to flow back into the anoxic tank from the aerobic tank; the sewage quantity is increased from 10L/d to 50L/d in an equivalent manner day by day, the daily increment is 10L/d, the return flow of the aerobic tank is increased from 20L/d to 100L/d in an equivalent manner day by day, the daily increment is 20L/d, the dissolved oxygen concentration in the aerobic tank is controlled to be 2mg/L, and the dissolved oxygen concentration in the anoxic tank is 0.3 mg/L.
Step five, stably treating sewage: and continuously feeding water and refluxing to remove nitrogen-containing pollutants in the sewage after the amplification culture of the microbial inoculum is completed.
The method of the embodiment is used for treating the municipal pipe network sewage, and the removal effect of the anoxic-aerobic process on the municipal pipe network sewage during the starting period is shown in the table.
TABLE 3
| Time (d) | Influent Ammonia nitrogen (mg/L) | Ammonia nitrogen (mg/L) of effluent | Total nitrogen (mg/L) of influent | Total nitrogen (mg/L) of effluent |
| 1 | 26.76 | 24.31 | 33.56 | 32.07 |
| 2 | 23.32 | 20.58 | 33.22 | 29.54 |
| 3 | 24.44 | 20.21 | 34.92 | 31.24 |
| 4 | 22.95 | 18.24 | 36.35 | 29.65 |
| 5 | 22.32 | 17.45 | 35 | 28.75 |
| 6 | 24.28 | 14.63 | 37.2 | 26.15 |
| 7 | 23.82 | 14.29 | 35.55 | 24.1 |
| 8 | 23.89 | 13.88 | 35.15 | 22.05 |
| 9 | 24.36 | 14.02 | 36.85 | 22.25 |
| 10 | 23.89 | 13.87 | 35.75 | 20.8 |
| 11 | 23.44 | 12.46 | 35.65 | 17.5 |
| 12 | 25.25 | 11.92 | 36.2 | 17.58 |
| 13 | 22.8 | 12.67 | 43.35 | 16.13 |
| 14 | 22.4 | 11.06 | 46.3 | 18.5 |
| 15 | 17.67 | 8.68 | 31.25 | 15.2 |
As can be seen from the table, the reduction speed of the ammonia nitrogen and the total nitrogen concentration of the effluent is higher in the first 6 days of operation, and then the ammonia nitrogen and the total nitrogen concentration of the effluent slowly decrease to be basically stable, which indicates that the biofilm formation can be basically completed in 6 days. In the 15d of operation, the ammonia nitrogen concentration of the effluent is reduced from 22-27mg/L to below 9 mg/L; the total nitrogen concentration is reduced from 30-47mg/L to below 15mg/L, and the concentration of each pollutant tends to be stable. The result shows that after 15 days of culture, the biomembrane on the surface of the carbon fiber in the anoxic-aerobic process is completely formed, the performance is stable, sludge discharge is not carried out when the process is operated for 30 days, and the water quality of effluent is close to the first-class A discharge standard of pollutant discharge Standard of urban sewage treatment plants.
Example 2
A quick start-up method of a biofilm system comprises the following process steps:
step one, preparing a culture environment: filling the anoxic tank and the aerobic tank with filler, and then filling the anoxic tank and the aerobic tank with sewage to be treated; the fillers suspended in the anoxic tank and the aerobic tank are carbon fiber fillers, and the densities of the fillers are both 400g/m2The effective volume of the anoxic pond is 15m in the embodiment3The effective volume of the aerobic tank is 45m3。
Step two, adding a microbial inoculum: adding 7.5kg of denitrifying bacteria agent into the anoxic tank, and adding 15kg of nitrifying bacteria agent into the aerobic tank; the denitrifying bacteria agent is a compound of pseudomonas stutzeri BNCC-221999, micrococcus luteus BNCC-139548, denitrifying Achromobacter BNCC-138371, a first biological enzyme and nutrient salt according to the mass ratio of 1:1:3:2: 1; the nitrifying agent is a compound of nitrosomonas CGMCC-11865, nitrobacteria CCTCC-M2019420, a second biological enzyme and nutrient salt according to the mass ratio of 3:2:1: 1. The first biological enzyme is prepared by blending nitrate reductase, nitrite reductase, nitric oxide reductase and nitrous oxide reductase according to the mass ratio of 2:2:1: 1; the second biological enzyme is a nitrifying enzyme.
Step three, dissolving, diffusing and aerating the microbial inoculum: after the denitrifying bacteria agent is added into the anoxic tank, the denitrifying bacteria agent is naturally dissolved and diffused in the anoxic tank, after the nitrifying bacteria agent is added into the aerobic tank, an aeration device in the aerobic tank is started to carry out stuffy aeration on the added nitrifying bacteria agent, and the dissolving, the diffusing and the stuffy aeration are carried out simultaneously for two days.
Step four, expanding and culturing the microbial inoculum: after dissolution, diffusion and stuffy aeration are finished, adding sewage into the anoxic tank, enabling the sewage to flow out after sequentially passing through the anoxic tank and the aerobic tank, adding the sewage into the anoxic tank, and simultaneously opening a backflow channel arranged between the aerobic tank and the anoxic tank to enable part of the sewage to flow back into the anoxic tank from the aerobic tank; the sewage amount is from 3m3D is increased to 15m day by equivalent3D, daily increment of 3m3D, the reflux of the aerobic tank is from 6m3D is increased to 30m day by equivalent3D, daily increment is 6m3During the period, the concentration of the dissolved oxygen in the aerobic pool is controlled to be 2mg/L, and the concentration of the dissolved oxygen in the anoxic pool is 0.3 mg/L.
Step five, stably treating sewage: and continuously feeding water and refluxing to remove nitrogen-containing pollutants in the sewage after the amplification culture of the microbial inoculum is completed.
The method of the embodiment is used for treating the river overflow sewage, and the removal effect of the process applied by the invention on the municipal pipe network sewage during the starting period is shown in the table.
TABLE 2
| Time (d) | Influent Ammonia nitrogen (mg/L) | Ammonia nitrogen (mg/L) of effluent | Water inlet assemblyNitrogen (mg/L) | Total nitrogen (mg/L) of effluent |
| 1 | 24.05 | 20.02 | 28.52 | 25.91 |
| 2 | 25.63 | 18.76 | 33.08 | 22.63 |
| 3 | 24.41 | 12.07 | 31.69 | 15.63 |
| 7 | 23.20 | 8.00 | 37.74 | 18.86 |
| 8 | 25.63 | 6.20 | 33.24 | 15.74 |
| 9 | 28.00 | 5.76 | 32.00 | 15.69 |
| 11 | 26.73 | 4.72 | 35.63 | 14.41 |
| 12 | 28.56 | 4.10 | 36.97 | 13.47 |
| 14 | 33.80 | 4.51 | 41.02 | 15.58 |
| 15 | 37.71 | 4.56 | 35.91 | 15.30 |
| 16 | 34.05 | 4.51 | 38.41 | 15.36 |
As can be seen from the table above, the reduction speed of the ammonia nitrogen and the total nitrogen concentration in the effluent is higher in the first 7 days of operation, and then the ammonia nitrogen and the total nitrogen concentration in the effluent slowly decrease to be basically stable, and the biofilm formation can be basically completed in 7 days. After 16d of culture, a biological film on the surface of the carbon fiber in the anoxic-aerobic process is completely formed, the performance is stable, and the concentration of the ammonia nitrogen in the effluent is reduced to below 5mg/L from 24-34 mg/L; the total nitrogen concentration is reduced from 28-41mg/L to below 16 mg/L.
Example 3
This example differs from example 1 in that the filler density of this example is 200g/m3In this embodiment, the concentration of dissolved oxygen in the aerobic tank is 2.5mg/L, and the sewage treatment effect of this embodiment is equivalent to that of embodiment 1.
Example 4
The difference between this example and example 1 is that the filler of this example is ecological grass with a density of 150g/m3In this embodiment, the concentration of dissolved oxygen in the aerobic tank is 1.5mg/L, the mass ratio of the return flow to the water inflow is 3:1, specifically, the amount of sewage in the first day of the embodiment is 10L/d, the amount of sewage is increased from 10L/d to 50L/d in an equivalent manner day by day, the daily increment is 10L/d, the amount of sewage in the first day of the embodiment is 30L/d, the amount of return flow of the aerobic tank is increased from 30L/d to 150L/d in an equivalent manner day by day, and the daily increment is 30L/d, and the sewage treatment effect of the embodiment is equivalent to the sewage treatment effect of the embodiment 1.
Example 5
The difference between this example and example 2 is that nylon fiber is used as the filler in this example, and the density is 400g/m3In this embodiment, the adding mass ratio of the denitrifying bacteria agent to the nitrifying bacteria agent is 1:3, specifically, the adding amount of the denitrifying bacteria agent in this embodiment is 5kg, and the adding amount of the nitrifying bacteria agent in this embodiment is 15 kg. The effect of sewage treatment in this example was comparable to that in example 2.
Example 6
The difference between this example and example 2 is that nylon fiber is used as the filler in this example, and the density is 400g/m3In this embodiment, the mass ratio of the return flow to the water inflow is 1.5:1, specifically, the amount of sewage in the first day of this embodiment is 4m3D, sewage amount is from 4m3D is increased to 20m day by equivalent3D, daily increment of 4m3D, the reflux of the aerobic tank is from 6m3D is increased to 30m day by equivalent3D, daily increment is 6m3And d. The stain of the present exampleThe water treatment effect was equivalent to that of example 2.
Example 7
The difference between this embodiment and embodiment 1 is that the ratio of the return flow of the nitrifying liquid to the water inflow is 3.5, the sewage amount on the first day of this embodiment is 10L/d, the sewage amount increases from 10L/d to 50L/d day by equivalent, and the daily increment is 10L/d, the sewage amount on the first day of this embodiment is 35L/d, the return flow of the aerobic tank increases from 35L/d to 175L/d day by equivalent, and the daily increment is 35L/d, at this time, the ratio of the return flow of the nitrifying liquid to the water inflow is too high, and the dissolved oxygen carried in the nitrifying liquid in the aerobic tank affects the content of the dissolved oxygen in the anoxic tank, so that the ammonia nitrogen concentration of the effluent of the municipal sewage decreases from 27mg/L to 13mg/L in 15 days of this embodiment, which is not better than the effect of embodiment 1.
Example 8
The difference between the embodiment and the embodiment 1 is that the ratio of the return flow rate of the nitrifying liquid to the water inlet rate of the nitrifying liquid in the embodiment is 1, at this time, the ratio of the return flow rate of the nitrifying liquid to the water inlet rate is too high, and the dissolved oxygen carried in the nitrifying liquid in the aerobic tank influences the content of the dissolved oxygen in the anoxic tank, so that the total nitrogen concentration of the municipal sewage is only reduced from 31mg/L to 25mg/L when the embodiment is implemented for 15 days, which is not better than the effect of the embodiment 1.
Example 9
This example is different from example 1 in that the concentration of the anoxic tank in this example is 0.7 mg/L. Because the dissolved oxygen concentration of the anoxic pond is too high, the activity of the denitrifying bacteria agent is reduced, and the amount of nitrate in the anoxic pond reduced into nitrogen is reduced, so that the total nitrogen concentration of effluent is increased, and when the anoxic pond is implemented for 15 days in the embodiment, the total nitrogen concentration of municipal sewage is only reduced from 31mg/L to 25mg/L, which is not equal to the effect of the embodiment 1.
Example 10
The difference between the present embodiment and embodiment 1 is that the dissolved oxygen concentration of the aerobic tank in the present embodiment is 1.0 mg/L. Because the concentration of dissolved oxygen in the aerobic tank is low, the activity of the nitrifying agent is influenced to a certain extent, so that the efficiency of converting ammonia nitrogen into nitrate is reduced, and the ammonia nitrogen treatment effect and the total nitrogen treatment effect are not better than those of the embodiment 1.
Comparative example 1
The technical solution of example 6 is described as comparative example 1 in patent application No. 201710051574.5.
Comparative example 2
Patent application No. 201610761797.6 describes the technical solution of example 1 as comparative example 2.
Comparing examples 1-2 of the present application with comparative examples 1-2, the conclusions are given in the following table:
TABLE 3
In addition, comparative examples 3 to 4 were set to demonstrate the effect of the selection of the nitrifying bacteria agent and the denitrifying bacteria agent of the present application.
Comparative example 3
Compared with the example 1, the denitrifying bacteria agent of the comparative example does not contain pseudomonas stutzeri, and the nitrifying bacteria agent does not contain nitrosomonas. Through verification, the starting time of the comparative example is 10 days, the impact strength capability is poor, and the influence caused by the change of the sewage concentration cannot be quickly adapted.
Comparative example 4
Compared with the example 1, the denitrifying bacteria agent of the comparative example does not add nutrient salt and the first biological enzyme, and the nitrifying bacteria agent does not add nutrient salt and the second biological enzyme. The comparative example was verified to have a start-up time of 12 days.
The above embodiments are preferred embodiments of the present application, and the protection scope of the present application is not limited by the above embodiments, so: all equivalent changes made according to the structure, shape and principle of the present application shall be covered by the protection scope of the present application.
Claims (11)
1. A method for rapid start-up of a biofilm system, comprising the following start-up steps:
step one, preparing a culture environment: filling the anoxic tank and the aerobic tank with filler, and then filling the anoxic tank and the aerobic tank with sewage to be treated;
step two, adding a microbial inoculum: adding a denitrifying bacterium agent into the anoxic tank, and adding a nitrifying bacterium agent into the aerobic tank;
step three, dissolving, diffusing and stuffy aeration of the microbial inoculum: after the denitrifying bacteria agent is added into the anoxic tank, the denitrifying bacteria agent is naturally dissolved and diffused in the anoxic tank, and after the nitrifying bacteria agent is added into the aerobic tank, an aeration device in the aerobic tank is started to perform stuffy aeration on the added nitrifying bacteria agent;
step four, expanding and culturing the microbial inoculum: after dissolution, diffusion and stuffy aeration are finished, adding sewage into the anoxic tank, enabling the sewage to flow out after sequentially passing through the anoxic tank and the aerobic tank, adding the sewage into the anoxic tank, and simultaneously opening a backflow channel arranged between the aerobic tank and the anoxic tank to enable part of the sewage to flow back into the anoxic tank from the aerobic tank;
step five, stably treating sewage: continuously feeding water and refluxing to remove nitrogen-containing pollutants in the sewage after the amplification culture of the microbial inoculum is completed;
wherein the sewage is municipal sewage or river overflow sewage;
wherein the denitrifying bacteria agent is a compound of pseudomonas stutzeri, micrococcus luteus, achromobacter denitrificans, a first biological enzyme and nutrient salt; the nitrifying agent is a compound of nitrosomonas, nitrobacteria, a second biological enzyme and nutrient salt.
2. A method of rapid start-up of a biofilm system according to claim 1, wherein: the denitrifying bacteria agent is a compound of pseudomonas stutzeri BNCC-221999, micrococcus luteus BNCC-139548, achromobacter denitrificans BNCC-138371, a first biological enzyme and nutrient salt according to the mass ratio of 1:1:3:2: 1; the nitrifying bacteria agent is a compound of nitrosomonas CGMCC-11865, nitrobacteria CCTCC-M2019420, a second biological enzyme and nutrient salt according to the mass ratio of 3:2:1: 1.
3. A method of rapid start-up of a biofilm system according to claim 2, wherein: the first biological enzyme is prepared by blending nitrate reductase, nitrite reductase, nitric oxide reductase and nitrous oxide reductase according to the mass ratio of 2:2:1: 1; the second biological enzyme is a nitrifying enzyme.
4. A method of rapid start-up of a biofilm system according to claim 1, wherein: the filler can adopt one of carbon fiber, ecological grass and nylon fiber.
5. A method of rapid start-up of a biofilm system according to claim 2, wherein: when the filler is carbon fiber, the density of the carbon fiber is 200-400g/m3(ii) a When the filler is ecological grass, the density of the ecological grass is 150-300g/m3(ii) a When the filler is nylon fiber, the density of the nylon fiber is 400-500g/m3。
6. A method of rapid start-up of a biofilm system according to claim 1, wherein: in the third step, the dissolving, diffusing and stuffy aeration time are both 1-2 days; in the fourth step, the time of the microbial inoculum expansion culture is 6-7 days.
7. A method of rapid start-up of a biofilm system according to claim 1, wherein: in the fourth step and the fifth step, the concentration of the dissolved oxygen in the anoxic pond is required to be lower than 0.5mg/L, and the concentration of the dissolved oxygen in the aerobic pond is 1.5-2.5 mg/L.
8. A method of rapid start-up of a biofilm system according to claim 1, wherein: in the fourth step and the fifth step, the mass ratio of the reflux quantity to the water inflow is (1.5-3): 1, the mass ratio of the water inflow to the water outflow is 1: 1.
9. A method of rapid start-up of a biofilm system according to claim 1, wherein: the COD of the sewage is less than 450 mg/L; the ratio of BOD/COD is 0.3-0.5; total nitrogen is less than 60 mg/L; the ammonia nitrogen is less than 50mg/L, and the total phosphorus is less than 6 mg/L.
10. A method of rapid start-up of a biofilm system according to claim 1, wherein: the mass ratio of the denitrifying bacteria agent to the nitrifying bacteria agent is 1 (2-3).
11. A method of rapid start-up of a biofilm system according to claim 1, wherein: the volume ratio of the anoxic tank to the aerobic tank is 1 (2-3).
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| CN113003723A (en) * | 2021-02-08 | 2021-06-22 | 清华大学 | Preparation method of coupled flora biofilm |
| CN115611464A (en) * | 2022-10-24 | 2023-01-17 | 墣锦环境工程（海南）有限公司 | A method for purifying the water quality of sewage outlets entering rivers |
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