CN115057523A - SBR wastewater treatment device and treatment method thereof - Google Patents
SBR wastewater treatment device and treatment method thereof 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
- C02F3/00—Biological treatment of water, waste water, or sewage
- C02F3/02—Aerobic processes
- C02F3/12—Activated sludge processes
- C02F3/1236—Particular type of activated sludge installations
- C02F3/1263—Sequencing batch reactors [SBR]
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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
- C02F3/34—Biological treatment of water, waste water, or sewage characterised by the microorganisms used
-
- C—CHEMISTRY; METALLURGY
- C02—TREATMENT OF WATER, WASTE WATER, SEWAGE, OR SLUDGE
- C02F—TREATMENT OF WATER, WASTE WATER, SEWAGE, OR SLUDGE
- C02F2101/00—Nature of the contaminant
- C02F2101/10—Inorganic compounds
- C02F2101/16—Nitrogen compounds, e.g. ammonia
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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
- C02F2101/00—Nature of the contaminant
- C02F2101/30—Organic compounds
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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
- C02F2101/00—Nature of the contaminant
- C02F2101/30—Organic compounds
- C02F2101/38—Organic compounds containing nitrogen
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- Y—GENERAL TAGGING OF NEW TECHNOLOGICAL DEVELOPMENTS; GENERAL TAGGING OF CROSS-SECTIONAL TECHNOLOGIES SPANNING OVER SEVERAL SECTIONS OF THE IPC; TECHNICAL SUBJECTS COVERED BY FORMER USPC CROSS-REFERENCE ART COLLECTIONS [XRACs] AND DIGESTS
- Y02—TECHNOLOGIES OR APPLICATIONS FOR MITIGATION OR ADAPTATION AGAINST CLIMATE CHANGE
- Y02W—CLIMATE CHANGE MITIGATION TECHNOLOGIES RELATED TO WASTEWATER TREATMENT OR WASTE MANAGEMENT
- Y02W10/00—Technologies for wastewater treatment
- Y02W10/10—Biological treatment of water, waste water, or sewage
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- Microbiology (AREA)
- Biodiversity & Conservation Biology (AREA)
- Hydrology & Water Resources (AREA)
- Engineering & Computer Science (AREA)
- Environmental & Geological Engineering (AREA)
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- Chemical & Material Sciences (AREA)
- Organic Chemistry (AREA)
- Purification Treatments By Anaerobic Or Anaerobic And Aerobic Bacteria Or Animals (AREA)
Abstract
The invention provides a SBR wastewater treatment device and a treatment method thereof, wherein the device comprises a raw water tank (1), a peristaltic pump (2) and an improved SBR device (5), wherein the raw water tank (1) is connected with the improved SBR device (5) through the peristaltic pump (2); waste water treatment device still includes the microorganism system of adding, the microorganism system of adding includes circulating pump (12) and microorganism fungus agent adds device (13), improved generation SBR device (5) link to each other with microorganism fungus agent adds device (13) through circulating pump (12), and microorganism fungus agent adds device (13) and communicates back improved generation SBR device (5) again. The invention is improved on the basis of the traditional SBR process, a microbial agent adding device is additionally arranged, and the added SDS microbial agent enters a microbial reaction zone of the improved SBR device to accelerate the proliferation of aerobic activated sludge.
Description
Technical Field
The invention belongs to the technical field of biological treatment of organic wastewater, and particularly relates to a SBR wastewater treatment device and a treatment method thereof.
Background
Sodium Dodecyl Sulfate (SDS) is a toxic and harmful chemical substance, is easily soluble in water, is widely applied to daily life and industrial production such as pharmacy, petroleum, papermaking, mining, textile, leather, printing and dyeing and the like, and is also one of important components of agricultural pesticides. Studies have shown that SDS at lower concentrations is not harmful to the environment, but at higher concentrations is harmful to varying degrees. For example, excessive SDS enters the natural water body, which endangers the growth and reproduction of fishes, bivalves and the like in the water body and inhibits the growth and photosynthetic capacity of beneficial algae and other aquatic plants in the water body. Along with the use of a large amount of SDS in production and life, a series of ecological environmental problems are brought about, and untreated high-concentration SDS wastewater is directly discharged into the natural environment, so that SDS can be continuously accumulated in the environment and even transferred between surface water and soil through water circulation, and further underground water is polluted.
At present, common methods for treating SDS in wastewater can be classified into physical methods (adsorption methods, ionizing radiation methods and the like) and chemical methods (catalysis methods, oxidation methods and the like), but in actual SDS sewage treatment, the physical methods and the chemical methods have high treatment cost, secondary pollution is easy to generate, and standard treatment of high-concentration SDS sewage is difficult to realize. Therefore, the method has the advantages of low development cost, no secondary pollution and high removal rate of the high-concentration SDS wastewater.
As an environment-friendly, low-cost and good-implementation-effect wastewater treatment method, the biological enhanced treatment has obvious advantages in the aspect of treating SDS (sodium dodecyl sulfate) pollution and is the main research direction of SDS wastewater treatment at present. However, SDS itself has a certain biological toxicity, and the biodegradability is poor, so that the effect of ordinary biological strengthening treatment is not ideal. In recent years, the research on bioaugmentation treatment of surfactants such as SDS by adding efficient degrading bacteria has been increasing. However, most of the SDS-degrading microorganisms screened at present are single bacterial strains, and the single bacterial strains have poor tolerance, are easy to pollute, have limited SDS wastewater treatment capacity and slow degradation rate, and are difficult to apply to actual SDS wastewater treatment. In the actual SDS wastewater environment, compared with a single SDS degrading bacterium, a microorganism union formed by multiple strains keeps the original population structure and diversity characteristics of the SDS degrading microorganism, and different contained bacterial species have synergistic effect, so that the SDS wastewater treatment method has stronger tolerance on high-concentration SDS wastewater and better treatment effect.
The Sequencing Batch Reactor (SBR) process utilizes degradation microorganisms attached to and growing on the surface of activated sludge to treat wastewater, and has the advantages of stable operation, small sludge yield, economy, energy conservation and the like. However, since SDS has biological toxicity and poor biodegradability, in the conventional SBR process, SDS is not only difficult to be degraded by the original microbial population in the biological treatment system, but also sometimes affects the removal effect of the system on other organic matters, and thus the treatment efficiency is reduced, so that the conventional SBR process can only be used for treating low-concentration wastewater (the initial concentration of SDS is less than 1000mg/L) with respect to surfactants having biological toxicity such as SDS, and the defects of long degradation time, poor sludge settling property, incomplete SDS degradation and the like exist, and the application of the SBR process to the treatment of high-concentration SDS wastewater has not been found for a while.
The invention is provided based on the background, and the traditional SBR process is not improved at present, so that the SDS is degraded by microorganisms and the interference of the SDS on other organic matters is eliminated.
Disclosure of Invention
The invention overcomes the defects and shortcomings in the background technology and provides an SBR wastewater treatment device and a treatment method thereof.
In order to solve the technical problems, the technical scheme provided by the invention is as follows:
an SBR wastewater treatment device comprises a raw water tank, a peristaltic pump and an improved SBR device, wherein the raw water tank is connected with the improved SBR device through the peristaltic pump; waste water treatment facilities still includes the microorganism interpolation system, the microorganism interpolation system includes circulating pump and microbial inoculum interpolation device, improved generation SBR device links to each other through circulating pump and microbial inoculum interpolation device, and microbial inoculum interpolation device communicates back to improved generation SBR device again.
The improved SBR device is additionally provided with a microbial agent adding device on the basis of a conventional SBR wastewater treatment device. By adding the microbial inoculum adding device and adding a certain amount of high-efficiency degradation microbial inoculum, the microorganism quantity and activity of the degradable SDS in the wastewater treatment system are enhanced, the microorganism domestication time in the system is shortened, the system is quickly started to operate, the high-efficiency and stable removal effect is achieved, the SDS degrading rate and the SDS removing efficiency of the system are improved, the impact load resistance of the high-concentration SDS wastewater of the system is enhanced, and the effluent quality is better improved.
Preferably, the improved SBR device is internally provided with a stirring paddle and an aeration head, the improved SBR device is externally provided with a stirrer, a blower and a gas flowmeter, the stirrer controls the stirring paddle, and the blower is connected with the aeration head through the gas flowmeter.
Preferably, the improved SBR device is provided with a water inlet, a mud valve, a drain valve, a backflow valve and a plurality of detection ports, wherein the water inlet is connected with the peristaltic pump, and the backflow valve is connected with the circulating pump;
the improved SBR device is cylindrical, and the distance between the detection ports is 60-80% of the height of the improved SBR device. The cylindrical SBR device has no edges and corners, smooth surface, good stability, difficult deformation, convenient cleaning and lower cost.
Preferably, the SBR high-concentration wastewater treatment device is used for treating high-concentration Sodium Dodecyl Sulfate (SDS) wastewater, and the maximum concentration of the high-concentration sodium dodecyl sulfate wastewater is 3000 mg/L.
Under the same technical concept, the invention also provides a treatment method of the SBR wastewater treatment device, which comprises the following steps:
(1) inoculating aerobic activated sludge in the improved SBR device, starting the improved SBR device, inputting the wastewater raw material in the raw water tank into the improved SBR device, and increasing the concentration of the wastewater raw material along with the starting of the improved SBR device;
(2) after the improved SBR device runs for a week, stopping water inflow when the water inflow of the raw material of the wastewater reaches 20 percent of the effective volume of the device; the raw material of the wastewater is mixed with the microbial agent in the microbial agent adding device and enters the improved SBR device;
(3) starting and operating the improved SBR device in a sequencing batch mode, finishing the periodic reaction, discharging the precipitated wastewater raw materials, and controlling the sludge settlement ratio to be between 15 and 30 percent, so that the improved SBR device enters the next period;
(4) further improving the concentration of the raw materials of the wastewater, repeating the steps (2) and (3) and carrying out the wastewater treatment by the SBR method.
Preferably, when the modified SBR device is started up in step (1), the carbon source is added to the wastewater raw material in the raw water tank, and the amount of the carbon source is gradually reduced until the carbon source is not added as the degradation rate of the modified SBR device is increased. The carbon source utilization rate of the microorganism is high, and the carbon source has simple chemical structure and small molecular weight. When organic wastewater pollution is treated, additional small-molecule carbon sources such as glucose, methanol, sodium acetate and the like are added, so that the growth and development of microorganisms are facilitated.
Preferably, the carbon source is sodium acetate and/or glucose. More preferably, the carbon source is sodium acetate, and the concentration of sodium acetate is 50 mg/L. The added glucose and sodium acetate can play a good promoting role in degrading organic matters by the strains, and the price of the sodium acetate is lower than that of the glucose and is a common carbon source in the actual treatment of the coking wastewater, so the sodium acetate is preferably used as the carbon source in the patent.
Preferably, when the modified SBR device is started in the step (1), the raw material concentration of the wastewater in the raw water tank is 100 mg/L; gradually increasing the concentration of the wastewater raw material to 1000mg/L along with the improvement of the degradation rate of the improved SBR device to more than 85%; and (4) further increasing the concentration of the raw materials of the wastewater from 1000mg/L to 3000mg/L step by step.
The starting process adopts the wastewater raw material with lower concentration, increases the organic load, realizes the proliferation of aerobic activated sludge, gradually increases the concentration of the wastewater raw material along with the starting operation of the improved SBR device, and realizes the high-efficiency treatment and discharge of the wastewater raw material with high concentration.
Preferably, the microbial agent in the step (2) is a mixed solution of sterilized activated carbon adsorbed microorganism union, and the microorganism union comprises Paraburkholderia papaibaeckea, with the preservation number of CCTCC M2022396. More preferably, the microbial consortium comprises Paraburkholderia pavonii and SDS a complex strain SDS1 screened by universal primers. Mixing the composite strain SDS1 and Parabaikholderia according to the ratio of 7:3, at the temperature of 30 ℃, the pH value of 7, the salinity of 0.05%, the liquid loading amount of 50%, the inoculation amount of 2%, and the rotating speed of a shaking table of 180 r.min -1 And the degradation rate of the microorganism complex H3 to SDS after 48 hours is 90.1 percent under the condition that the additional nitrogen source is sodium nitrate and ammonium chloride and the initial concentration of SDS is 1600 mg/L.
Preferably, during the start-up and operation of the modified SBR apparatus in steps (1), (2) and (3), the SDS, COD, TN and NH of the effluent water of the plurality of detection ports are respectively measured 3 N concentration and real-time monitoring of the temperature, pH and DO concentration of the reaction system. More preferably, during the start-up and operation of the modified SBR system, the sludge shape and the types of the primary and secondary animals are periodically observed to determine whether or not the aeration amount is sufficient.
Preferably, the improved SBR device is started and operated in the step (3) in a sequencing batch mode, the operation period is 24 hours, wherein water is fed for 0.5 hour, aeration is carried out for 22 hours, sedimentation is carried out for 1 hour, and water and sludge are replaced for 0.5 hour; the water is drained once a day, the water drainage quantity is 1000-1500mL, the sludge is drained once a day, and the sludge drainage quantity is 200-300 mL.
Preferably, the modified SBR device is started and operated in a sequencing batch mode in the step (3), and a defoaming agent containing silicone oil is added during the operation of the modified SBR device; when water feeding is stopped, adding the microbial agent in an amount of 2% (volume ratio)
The high-efficiency defoaming agent with silicone oil as a basic component is added to prevent the SBR biochemical system from collapsing due to foam expansion.
Compared with the prior art, the invention has the beneficial effects that:
(1) the invention is improved on the basis of the traditional SBR process, a microbial agent adding device is additionally arranged, and the added SDS microbial agent enters a microbial reaction zone of the improved SBR device to accelerate the proliferation of aerobic activated sludge. After aerobic sludge is cultured and matured, the degradation rate of SDS with the concentration of 3000mg/L in an improved SBR reaction system reaches 91.1 percent within 24 hours. Compared with the traditional activated sludge system without adding the microbial agent, the aerobic activated sludge has higher tolerance concentration (the tolerance capacity is about 3 times that of the traditional activated sludge system) and higher degradation rate (about 2 times that of the traditional activated sludge system).
(2) The invention not only has better degradation capability to high-concentration SDS, but also has good denitrification and carbon removal effects to the washing wastewater containing SDS. In the improved SBR reaction system, after 24 hours, the reaction is carried out on COD, TN and NH 3 - The removal rates of N reach 89.5%, 75.3% and 91.9% respectively.
(3) According to the method, the traditional SBR process is improved, the microbial agent is applied to the rapid removal of the high-concentration SDS, the high-concentration SDS wastewater can be rapidly degraded by adopting the method, and the method has a good application prospect in the actual treatment of the washing wastewater containing the high-concentration SDS.
Drawings
In order to more clearly illustrate the embodiments of the present invention or the technical solutions in the prior art, the drawings used in the description of the embodiments or the prior art will be briefly described below, and it is obvious that the drawings in the following description are some embodiments of the present invention, and for those skilled in the art, other drawings can be obtained according to these drawings without creative efforts.
FIG. 1 is a schematic view showing the construction of an SBR-process wastewater treatment apparatus in example 1;
FIG. 2 is a graph of the protozoa observed in the aerobic activated sludge acclimatized to the stationary phase sludge in example 1;
FIG. 3 shows the growth pattern of the SDS-highly degrading bacterium D2 in example 1 on LB selective medium;
FIG. 4 shows the degradation rate of the modified SBR apparatus of example 1 at an initial SDS concentration of 3000 mg/L;
FIG. 5 is a classification of dominant groups of activated sludge microorganisms in the modified SBR apparatus before and after microbial agent addition in example 1;
FIG. 6 shows the removal rates of COD, TN and NH3-N in the modified SBR apparatus of example 1 under the condition of SDS initial concentration of 3000 mg/L;
in the figure: 1. a raw water tank; 2. a peristaltic pump; 3. a water inlet; 4. a stirrer; 5. an improved SBR apparatus; 6. a stirring paddle; 7. a first detection port; 8. a second detection port; 9. a mud valve; 10. a drain valve; 11. a reflux valve; 12. a circulation pump; 13. A microbial agent addition device; 14. a blower; 15. a gas flow meter; 16. an aeration head.
Detailed Description
In order to facilitate understanding of the invention, the invention will be described more fully and in detail with reference to the accompanying drawings and preferred embodiments, but the scope of the invention is not limited to the specific embodiments below.
Unless otherwise defined, all terms of art used hereinafter have the same meaning as commonly understood by one of ordinary skill in the art. The terminology used herein is for the purpose of describing particular embodiments only and is not intended to limit the scope of the present invention.
Unless otherwise specifically stated, various raw materials, reagents, instruments, equipment and the like used in the present invention are commercially available or can be prepared by existing methods.
Example 1:
the SBR wastewater treatment device of the embodiment:
as shown in figure 1, the SBR wastewater treatment device comprises a raw water tank 1, a peristaltic pump 2 and a modified SBR device 5, wherein the raw water tank 1 is connected with the modified SBR device 5 through the peristaltic pump 2; the microorganism adding system comprises a circulating pump 12 and a microorganism bacterium agent adding device 13, the improved SBR device 5 is connected with the microorganism bacterium agent adding device 13 through the circulating pump 12, and the microorganism bacterium agent adding device 13 is communicated back to the improved SBR device 5.
Improved generation SBR device 5 is equipped with water inlet 3, mud valve 9, drain valve 10, return valve 11 and first detection mouth 7, second detection mouth 8, and water inlet 3 links to each other with peristaltic pump 2, and return valve 11 links to each other with circulating pump 12.
Improved generation SBR device 5 is cylindrical, and first detection mouth 7, second detection mouth 8 interval are 80 mm. The improved SBR device 5 has the inner diameter of 200mm and the height of 580mm, is made of organic glass and has the effective volume of 20L; the effective volume of the raw water tank 1 is 100L, and the inner diameters of the water inlet 3, the return valve 11, the first detection port 7, the second detection port 8, the drain valve 10 and the mud valve 9 are 20 mm.
After the SBR wastewater treatment device is assembled, firstly inoculating activated sludge into an improved SBR device 5; waste water in the raw water tank 1 enters an improved SBR device 5 through a water inlet 3 at the top end of the device by utilizing a peristaltic pump 2; meanwhile, the blower 14 blows air into the improved SBR device 5 through the gas flowmeter 15 and the aerator 16 to provide sufficient dissolved oxygen for the growth and development of microorganisms; the returned sludge is connected with a microbial agent adding device 13 through a return valve 11 and a circulating pump 12, and the microbial agent is efficiently degraded and enters the improved SBR device 5; after the reaction period is finished, the water body after the original sewage treatment flows out from the drain valve 10, and the residual sludge is discharged from the sludge discharge valve 9.
The SBR wastewater treatment method of the embodiment comprises the following steps:
SDS simulation wastewater with the concentration of 100mg/L is added into the improved SBR device, sodium acetate with the concentration of 50mg/L is added as an auxiliary carbon source, and the SBR reaction system is started in a sequencing batch mode. After the reactor is started, the sludge properties and the species of the primary and secondary animals are regularly observed through sampling ports with different heights, whether the aeration amount is sufficient or not is judged, the SDS concentration of effluent is determined, and the operation condition of the reactor is analyzed, so that corresponding adjustment is carried out. After the reactor runs for a week, gradually reducing the adding amount of sodium acetate along with the continuous improvement of the degradation rate of the SDS of the system until the SDS is used as a unique carbon source; gradually increasing the SDS concentration of the simulated wastewater inlet water from 100mg/L to 1000mg/L, increasing the organic load and realizing the proliferation of the aerobic activated sludge. During the starting period of the improved SBR device, the operation period is 24 hours, the water inlet time is 0.5 hour, the aeration time is 22 hours, the sedimentation time is 1 hour, the water changing and sludge discharging time is 0.5 hour, the sedimentation ratio is recorded, the water is discharged once a day, the water discharge amount is 1500mL, the sludge is discharged once a day, and the sludge discharge amount is 200 mL and 300 mL.
The result shows that the aerobic activated sludge is gradually matured along with the improvement of the SDS treatment capacity of the reaction system.
As shown in fig. 2, protozoa observed by a microscope during sludge acclimation were observed, and in the initial stage of sludge acclimation, a small gloriomydia (v. microsoma) was observed (fig. 2a), which is a saprophytic protozoa and survived under extreme environmental conditions such as high pollutant load, and the environmental conditions for water invasion marked by mass propagation of small gloriomydia were severe, which is consistent with the biotoxicity of SDS wastewater. With continuous domestication of aerobic activated sludge, the main groups of protozoan communities are changed. In the sludge acclimation middle stage, the tenons (Spirostomum) can be observed through fig. 2b, and tenons (Aspidisca) can be observed through fig. 2c, and the occurrence of a large number of the tenons and tenons indicates that the content of dissolved oxygen in water is high, the sludge sedimentation performance is good, and the condition indicates that the pollutant load in the system gradually tends to a normal level from a high level. When aerobic activated sludge is cultured to be mature, rotifers (Rotaria) can be observed as an animal which is a planktonic protozoon through a graph 2d, the appearance of a large amount of rotifers indicates that effluent pollutants are low in load and good in water quality, and the acclimation of the aerobic activated sludge is proved to be mature.
Preparing a microbial agent for efficiently degrading SDS:
the SDS efficient degrading bacteria D2 mentioned in the application is classified and named as Para herborickholeria D2(Para burkholderia tropica D2), the preservation number is CCTCC M2022396, and the preservation numbers are preserved in China center for type culture Collection, and the preservation unit addresses are as follows: in Wuhan university school of Wuhan 299 eight-channel in Wuhan district, Wuhan city, Hubei, the preservation time is 2022, 04 months and 08 days.
(1) Screening of SDS Complex strains
50mL of the collected muddy water sample NS1 was put in a sterilized 100mL flask, and SDS was added thereto so that the concentration thereof was 100 mg.L -1 Then re-activated, and inoculated in the initial concentration of 100 mg.L after activation -1 In an SDS inorganic salt medium. Taking SDS as a unique carbon source, inoculating 2 percent of bacteria, culturing at 30 ℃ and a shaking table rotating speed of 180 r.min < -1 > to carry out gradient acclimation and culture, measuring the content of the SDS in a shaking bottle after culturing for 48 hours, and screening to obtain a complex bacteria system SDS 1. Each experiment was repeated 3 times, and SDS inorganic salt medium without inoculated bacteria solution was used as a blank. After the gradient acclimatization, the degradation rate of the composite bacterial system SDS1 to SDS reaches 89.5 percent, and compared with that before the gradient acclimatization, the degradation rate is reduced by 5.0 percent, but the degradation capability to SDS is from 100 mg.L -1 Increased to 1600 mg.L -1 The gradient domestication is shown to effectively improve the degradation capability of the composite bacterial system SDS1 on SDS.
(2) Separation, purification, domestication and stability determination of SDS (sodium dodecyl sulfate) high-efficiency degrading bacteria
Taking 10 of SDS degradation complex strain SDS1 -4 、10 -5 、10 -6 And uniformly coating the gradient diluent on an SDS inorganic salt culture medium, culturing for 48h at the constant temperature of 30 ℃, selecting a single colony for plate streaking after the bacteria grow in a culture dish, selecting the bacteria after streaking for purification culture, then inoculating the bacteria to LB for culture until logarithmic phase, and then transferring the bacteria to the SDS inorganic salt culture medium. And continuously increasing the SDS domestication concentration until the degrading bacteria with the highest tolerance concentration are screened. And selecting SDS degrading bacteria with highest concentration and highest degradation rate after domestication for passage, carrying out passage for 15 times in an SDS inorganic salt culture medium with the highest tolerance concentration, detecting the content of SDS after each passage, and taking the degrading bacteria with good stability after 15 passages as subsequent experimental strains to be recorded as the high-efficiency SDS degrading bacteria D2. FIG. 3 shows the microscopic pattern of strain D2And (4) state characteristics.
(3) Preparation of bacterial suspension of SDS (sodium dodecyl sulfate) microbial agent capable of efficiently degrading
Mixing SDS1 and D2 at a ratio of 7:3, wherein the initial concentration of SDS is 1600 mg.L -1 Inoculating to 30 deg.C, pH 7, salinity 0.05%, inoculation amount 2%, liquid loading 50%, and table rotation speed 180 r.min -1 Culturing in the inorganic salt culture medium for 48H to obtain microorganism complex H3, and placing the bacterial liquid cultured in 100mL of inorganic salt into 100mL of sterile centrifuge tube twice at 10000 r.min -1 Centrifuging for 5min under the condition, discarding supernatant, washing the centrifuged and concentrated thallus with sterile water into 2mL sterilized PE tube at 10000 r.min -1 Centrifuging for 2min under the condition, discarding supernatant, and storing to 5mL sterilized PE tube with constant volume of concentrated thallus to ensure OD of bacterial suspension 600 Around 2.500. Each set of experiments was repeated 3 times.
(4) Preparation of microbial agent
Mixing 50mL of prepared bacterial suspension of the efficient degradation microbial agent with 1g of sterilized activated carbon powder, and then carrying out shaking table rotation speed 180 r-min at the temperature of 30 DEG C -1 And (4) fixing for 12h to obtain the SDS microbial agent. Each set of experiments was repeated 3 times.
Degradation of SDS by the improved SBR device:
after the modified SBR device is stably started for one week, the initial concentration of SDS in the inlet water of the device is gradually increased from 1000mg/L to 3000 mg/L. In the operation process, the operation period is 24 hours, wherein the water feeding is 0.5 hour, the aeration is 22 hours, the sedimentation is 1 hour, and the water changing and sludge discharging are 0.5 hour. When water inflow is finished, a microbial agent for efficiently degrading SDS is added through a microbial agent adding device 13, and the adding amount is 2% (volume ratio). And the added SDS microbial agent is mixed with the returned sludge and then enters a microbial reaction zone of the improved SBR device (5).
As shown in FIG. 4, the degradation rate of SDS in simulated wastewater with concentration as high as 3000mg/L in 24h by the improved SBR device added with microbial agent reaches 91.4%. Compared with the traditional SBR activated sludge system without adding the microbial agent, the aerobic activated sludge in the embodiment has higher tolerance concentration (about 3 times of that of the traditional SBR activated sludge system) and faster degradation rate (about 2 times of that of the traditional SBR activated sludge system).
Bacterial community composition and relative abundance of the improved SBR device:
the following results were obtained by subjecting activated sludge samples before and after the addition of the microbial agent to the improved SBR apparatus to DNA extraction, library construction, sequencing, macrogenomics analysis, and comparison with the Blast + (Version: 2.10.0) database of NCBI.
The dominant population at the phylum level of bacterial high-throughput sequencing is shown in FIG. 5A, and is Proteobacteria (Proteobacteria), Actinobacillus (Actinobacillus) and Bacteroides (Bacteroides) in the order of average abundance. On the genus level, the ratio of the microbial species Burkholderia, unclassified _ Burkholderia which have the effect of degrading the SDS in the activated sludge before the microbial agent is added is only 3.01%, and after the high-concentration SDS wastewater is treated according to the methods described in examples 2 and 4, as can be seen from fig. 5B, the dominant genera in the activated sludge are significantly different, wherein the ratio of Burkholderia, unclassified _ Burkholderia is increased to 31.30%. The added microbial agent can be colonized in the improved SBR reactor, the dominant group of the microbes in the activated sludge is changed, and the high-efficiency removal of the SDS is realized.
Removal effect of improved SBR (sequencing batch reactor) reaction system on COD (chemical oxygen demand), TN (total nitrogen) and NH3-N of simulated wastewater
The simulated wastewater with an initial SDS concentration of 3000mg/L had an initial COD concentration of 14000ppm, a TN concentration of 2240ppm and an NH3-N concentration of 1840 ppm.
As shown in FIG. 6, the removal rates of the improved SBR device added with the microbial agent to simulated wastewater COD, TN and NH3-N with the concentration of 3000mg/L within 24h reach 89.5%, 75.3% and 91.9% respectively.
This example illustrates that mature aerobic activated sludge inoculated with SDS microbial inoculum can rapidly and efficiently degrade waste water containing high-concentration SDS in a short time in a modified SBR device, and has good denitrification and decarbonization effects.
Claims (10)
1. An SBR wastewater treatment device comprises a raw water tank (1), a peristaltic pump (2) and an improved SBR device (5), wherein the raw water tank (1) is connected with the improved SBR device (5) through the peristaltic pump (2); the improved SBR device is characterized by further comprising a microorganism adding system, wherein the microorganism adding system comprises a circulating pump (12) and a microorganism bacterium agent adding device (13), the improved SBR device (5) is connected with the microorganism bacterium agent adding device (13) through the circulating pump (12), and the microorganism bacterium agent adding device (13) is communicated back to the improved SBR device (5); the SBR high-concentration wastewater treatment device is used for treating high-concentration lauryl sodium sulfate wastewater, and the highest concentration of the high-concentration lauryl sodium sulfate wastewater is 3000 mg/L.
2. The SBR wastewater treatment device of claim 1, wherein the improved SBR device (5) is internally provided with a stirring paddle (6) and an aeration head (16), and externally provided with a stirrer (4), a blower (14) and a gas flow meter (15), the stirrer (4) controls the stirring paddle (6), and the blower (14) is connected with the aeration head (16) through the gas flow meter (15).
3. The SBR method wastewater treatment device as claimed in claim 1, wherein the improved SBR device (5) is provided with a water inlet (3), a mud valve (9), a drain valve (10), a return valve (11) and a plurality of detection ports, the water inlet (3) is connected with the peristaltic pump (2), and the return valve (11) is connected with a circulating pump (12); the improved SBR device (5) is cylindrical, and the distance between the plurality of detection openings is 60-80% of the height of the improved SBR device (5).
4. The treatment method of the wastewater treatment plant of SBR process as claimed in any one of claims 1 to 3, comprising the steps of:
(1) inoculating aerobic activated sludge in the improved SBR device (5), starting the improved SBR device (5), inputting the wastewater raw material in the raw water tank (1) into the improved SBR device (5), and increasing the concentration of the wastewater raw material along with the starting of the improved SBR device (5);
(2) after the improved SBR device (5) runs for a week, stopping water inflow when the water inflow of the wastewater raw material reaches 20 percent of the effective volume of the device; the raw material of the wastewater is added into a device (13) by a microbial agent, mixed with the microbial agent and enters an improved SBR device (5);
(3) starting and operating the improved SBR device (5) in a sequencing batch mode, finishing the periodic reaction, draining after the wastewater raw material is precipitated, and controlling the sludge settling ratio to be 15-30%, so that the improved SBR device (5) enters the next period;
(4) further improving the concentration of the raw materials of the wastewater, repeating the steps (2) and (3) and carrying out the wastewater treatment by the SBR method.
5. The process according to claim 4, wherein in the step (1), when the modified SBR apparatus (5) is started, a carbon source is added into the wastewater raw material in the raw water tank (1), and the carbon source is gradually reduced until the carbon source is not added along with the increase of the degradation rate of the modified SBR apparatus (5); the carbon source is sodium acetate and/or glucose.
6. The process according to claim 4, wherein in step (1), when starting up the modified SBR apparatus (5), the raw water tank (1) has a raw water concentration of 100 +/-20 mg/L; gradually increasing the concentration of the raw material of the wastewater to 1000 +/-100 mg/L along with the increase of the degradation rate of the improved SBR device (5) to more than 85%; in the step (4), the concentration of the raw materials for further improving the wastewater is gradually improved from 1000 +/-100 mg/L to 3000 +/-200 mg/L.
7. The process of claim 4, wherein in step (2) the microbial inoculant is a mixture of sterilized activated carbon-adsorbed microbial consortium comprising the bacterium Parabracter Holeria, deposit number CCTCC M2022396.
8. The method according to claim 4, wherein SDS, COD, TN, NH of effluent water from a plurality of detection ports are measured during the start-up and operation of the modified SBR apparatus (5) in steps (1), (2) and (3) 3 N concentration and real-time monitoring of temperature, pH and DO concentration of the reaction systemAnd (4) degree.
9. The process of claim 4, wherein the modified SBR apparatus (5) is started and operated in a sequencing batch mode in the step (3) for 24 +/-1 h, wherein the water feeding is performed for 0.5 +/-0.1 h, the aeration is performed for 22 +/-1 h, the sedimentation is performed for 1 +/-0.1 h, and the water changing and sludge discharging are performed for 0.5 +/-0.1 h; the water is drained once a day, the water drainage quantity is 1500mL once a day, the mud drainage quantity is 200 mL once a day, and the mud drainage quantity is 300mL once a day.
10. The process according to claim 4, characterized in that in step (3) the modified SBR unit (5) is started up and operated in a sequencing batch mode, during the operation of the modified SBR unit (5), a defoaming agent containing silicone oil is added; when water feeding is stopped, adding the microbial agent in an amount which is 2 +/-0.5 percent of the volume ratio of the effective volume of the device.
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