CN116119838A - Method for enhancing pyridine degradation and synchronous short-range denitrification by combining functional bacteria with MABR (mechanical anaerobic fermentation) technology - Google Patents
Method for enhancing pyridine degradation and synchronous short-range denitrification by combining functional bacteria with MABR (mechanical anaerobic fermentation) technology Download PDFInfo
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Abstract
The invention discloses a method for enhancing synchronous short-range denitrification of pyridine degradation by combining functional bacteria with MABR technology. According to the ecological niche characteristics of the biological film in the MABR technology, the pyridine degradation function strain rhizobium NJUST18 inoculum, nitrified sludge and denitrification function strain paracoccus denitrificans NJUST53 inoculum are sequentially subjected to film formation. The rhizobium of the aerobic layer in the biofilm formed after the film is formed grows by taking pyridine as a sole carbon source and a nitrogen source, and nitrifying bacteria utilize ammonia nitrogen generated by pyridine degradation to carry out the nitrifying process. The denitrifying paracoccus of the anoxic layer uses nitrite nitrogen/nitrate nitrogen generated in the nitration process to carry out denitrification and denitrification by pyridine. In addition, the aeration pressure and the pH of the inlet water are controlled to inhibit the activity of nitrite oxidizing bacteria, so that synchronous short-range denitrification of enhanced pyridine degradation is realized.
Description
Technical Field
The invention belongs to the technical field of biological treatment of environmental organic pollutants, relates to a method for strengthening pyridine degradation and synchronous short-range denitrification by combining functional bacteria with an MABR (mechanical fermentation process), and in particular relates to a method for strengthening volatile pyridine degradation and synchronous short-range denitrification by combining two functional strains with an MABR process.
Background
As a typical nitrogen-containing heterocyclic compound, pyridine is widely applied to industries such as medical manufacturing, agriculture, printing and dyeing industry, coking industry, explosive production and the like, and a large amount of pyridine wastewater with the characteristic of low C/N ratio is generated. Biological treatment is considered to be a low-cost, environmentally friendly wastewater treatment technology. Among them, anaerobic treatment is generally limited due to low removal rate and poor process stability, and conventional aerobic treatment processes are not only energy-consuming for treatment of volatile pyridine wastewater, but also cause nausea odor and serious air pollution. In addition, with the degradation of pyridine, nitrogen on the pyridine ring can be finally released into the water environment in the form of ammonia nitrogen, so that secondary pollution is caused.
The membrane aeration biological membrane reactor (Membrane Aerated Biofilm Reactor, MABR) is a sewage high-efficiency treatment technology combining membrane technology and biological membrane technology. The unique microbial layered structure and electrochemical gradient of the biofilm formation in the MABR system can simultaneously exist an aerobic zone, an anoxic zone and an anaerobic zone, and provides favorable conditions for synchronous short-cut nitrification and denitrification. In addition, MABR has the advantages of bubble-free aeration and high oxygen utilization efficiency, so that the problem that volatile organic compounds are easy to volatilize in the traditional aerobic treatment process is solved.
In recent years, the use of MABR in wastewater treatment has been of great interest, however, currently most of MABR is applied to wastewater having high nitrogen characteristics and low toxicity (e.g., municipal wastewater, livestock wastewater, etc.). For example, wang Biwei et al utilized a membrane aeration biofilm reactor to treat domestic sewage (Wang Biwei. Research on treatment of domestic sewage by a membrane aeration biofilm reactor [ D ] university of chinese technology, 2018.), zhang et al utilized a membrane aeration biofilm reactor to treat cow dung anaerobic fermentation broth (Zhang. Cow dung stone crystallization combined with a membrane aeration biofilm reactor to treat cow dung anaerobic fermentation broth [ D ] university of harbine industry, 2018.), sun Qiuhui et al utilized a membrane aeration biofilm reactor to treat black and odorous river water (Sun Qiuhui. Research on oxygen increasing and quality improving effects of black and odorous water body by bubble type MABR technology, and optimum design [ D ]. University of Tianjin, 2018.). The use of MABR in highly toxic chemical wastewater remains limited.
Disclosure of Invention
Aiming at the problems of pyridine volatilization pollution caused by aeration and oxygen supply in a pyridine aerobic biological treatment system and difficult denitrification of low carbon nitrogen ratio wastewater, the invention provides a method for enhancing pyridine degradation and synchronous short-range denitrification by combining functional bacteria with MABR technology.
The technical scheme of the invention is as follows:
the method for strengthening pyridine degradation and synchronous short-range denitrification by combining functional bacteria with MABR technology comprises the following specific steps:
(1) After the rhizobium NJUST18 is subjected to expansion culture, liquid bacteria are centrifuged, residual nutrients are removed by washing, bacterial sediment obtained by centrifugation is used as bacterial inoculum, then the bacterial sediment is injected into an MABR (MABR reactor along with pyridine wastewater inflow, continuous inflow is carried out after internal circulation is maintained for 3-4 days, a compact biological film is gradually formed on a fiber film in the reactor, and finally the bacterial inoculum sinking at the bottom of the reactor is discharged out of the system;
(2) After the pyridine removal rate of the reactor is stable, the nitrified sludge acclimatized by the ammonia nitrogen wastewater is injected into the MABR reactor, continuous flow water inflow is carried out after internal circulation is maintained for 3-4 days, a new layer of biological film is gradually covered on the biological film, and finally, the nitrified sludge sunk at the bottom of the reactor is discharged out of the system;
(3) Centrifuging liquid bacteria after the expansion culture of the paracoccus denitrificans NJUST53, cleaning to remove residual nutrient substances, centrifuging again to obtain bacterial sediment serving as bacterial inoculum, injecting the bacterial sediment into the MABR (MABR reactor along with the inlet water after the removal rate of pyridine and ammonia nitrogen by the reactor is stable, carrying out continuous flow inlet after maintaining the internal circulation for 3-4 d, gradually covering a layer of new biological film on the biological film, and finally discharging the bacterial inoculum sinking at the bottom of the reactor out of the system;
(4) The aeration pressure and the pH value of the inlet water are respectively controlled at 0.02+/-0.005 MPa and 8.0-8.2, and synchronous short-range denitrification of pyridine degradation is realized by using MABR.
In the step (1), the rhizobium NJUST18 is preserved in China Center for Type Culture Collection (CCTCC) in the 3 rd month of 2013, and the preservation number is CCTCC NO: m2013110, the preservation address is the university of Wuhan in Wuhan, hubei province of China and is fully disclosed in Chinese patent ZL 201310553435.4.
In the step (3), the paracoccus denitrificans NJUST53 is preserved in China Center for Type Culture Collection (CCTCC) in the year 2022, and the strain preservation numbers are CCTCC NO: m2022178, the preservation address is the university of Wuhan in Wuhan, hubei province, china, and is fully disclosed in Chinese patent application 202210608230.0.
In the specific embodiment of the invention, in the step (1), the specific method for the amplification culture of the rhizobium NJUST18 comprises the following steps: rhizobium NJUST18 is inoculated into an inorganic salt culture medium MSM added with 1g/L pyridine, and shake cultivation is performed for more than 96 hours.
In the specific embodiment of the invention, in the step (3), the specific method for amplifying and culturing the paracoccus denitrificans NJUST53 comprises the following steps: paracoccus denitrificans NJUST53 was inoculated into an inorganic salt medium MSM to which 1g/L glucose was added, and shake-cultured for 96 hours or more.
In a specific embodiment of the invention, the composition of the inorganic salt medium MSM is: na (Na) 2 HPO 4 ·2H 2 O 3.5g/L，KH 2 PO 4 1g/L，(NH4) 2 SO 4 500mg/L，MgCl 2 ·6H 2 O 100mg/L，Ca(NO 3 ) 2 ·4H 2 O
50mg/L, trace element SL-4.0 ml/L; wherein the composition of the trace elements SL-4 is as follows: EDTA0.5g/L FeSO 4 ·7H 2 O 0.2g/L，ZnSO 4 ·7H 2 O 0.001g/L，MnCl 2 ·4H 2 O 0.003g/L，H 3 BO 4 0.03g/L，CoCl 2 ·6H 2 O 0.02g/L，CuCl 2 ·2H 2 O 0.001g/L，NiCl 2 ·6H 2 O 0.002g/L，Na 2 MoO 4 ·2H 2 O0.003g/L。
In a specific embodiment of the invention, in the step (1), (2) or (3), the centrifugation speed is 8000 rpm, the centrifugation time is 10min, and the cleaning solution is phosphate buffer solution.
The method for strengthening pyridine degradation and synchronous short-range denitrification by combining the functional bacteria with the MABR technology can strengthen the degradation of pyridine and the removal of nitrogen in a single reactor. The pyridine degradation functional strain rhizobium NJUST18, nitrified sludge and paracoccus denitrificans NJUST53 are used as inoculums, membrane hanging is carried out according to a microbial ecological niche, and efficient degradation of pyridine and efficient removal of nitrogen are realized by utilizing the synergistic effect among pyridine degradation bacteria, nitrified bacteria and denitrified bacteria.
Compared with the prior art, the invention has the following remarkable advantages:
according to the invention, two functional strains are combined with MABR for the first time, and each functional strain lives on a respective ecological niche, so that the degradation of pyridine and the removal of nitrogen are enhanced. The invention is directed to 0.15 kg.m -3 ·d -1 The pyridine of the method can be completely removed, the TN removal rate is up to 95.24%, and the TOC removal rate is up to 94.88%. The invention effectively solves the problems of easy volatilization of pyridine, difficult denitrification of low carbon ratio waste water, large occupied area of the traditional aerobic-anoxic process and the like in the traditional aerobic process, and has industrial practicability.
Drawings
FIG. 1 shows the effect of a symbiotic system of two functional strains and nitrified sludge on pyridine degradation and denitrification using a conventional oxygen supply mode, (a) shows a change in pyridine concentration, (b) shows a change in trisnitrogen concentration, and (c) shows TN and TOC removal rates.
FIG. 2 is a schematic diagram of a dedicated apparatus for a pyridine wastewater treatment process.
FIG. 3 is a graph showing the effect of two functional strains on pyridine removal by MABR combined technology.
FIG. 4 is a graph showing the change in ammonia nitrogen, nitrite nitrogen and nitrate nitrogen concentration in effluent of two functional strains combined MABR process.
FIG. 5 is a graph showing the TOC removal effect of two functional strains combined with MABR.
FIG. 6 is a graph showing the effect of two functional strains on TN removal by MABR process.
Biological preservation information
The rhizobium NJUST18 disclosed by the invention is preserved in China Center for Type Culture Collection (CCTCC) in the year 3 and 28 of 2013, and the preservation number is CCTCC NO: m2013110, the preservation address is the university of Wuhan in Wuhan, hubei province of China and is fully disclosed in Chinese patent ZL 201310553435.4.
The Paracoccus denitrificans NJUST53 is preserved in China Center for Type Culture Collection (CCTCC) in 2022, and the strain preservation numbers are CCTCC NO: m2022178, the preservation address is the university of Wuhan in Wuhan, hubei province, china, and is fully disclosed in Chinese patent application 202210608230.0.
Detailed Description
The invention will be described in further detail with reference to specific embodiments and drawings.
In the following examples and comparative examples, the compositions of the culture medium and simulated wastewater used were as follows:
the inorganic salt culture medium MSM comprises the following components: na (Na) 2 HPO 4 ·2H 2 O 3.5g/L，KH 2 PO 4 1g/L，(NH4) 2 SO 4 500mg/L，MgCl 2 ·6H 2 O 100mg/L，Ca(NO 3 ) 2 ·4H 2 O50 mg/L, trace element SL-4
1.0ml/L。
The pyridine simulated wastewater comprises the following components: pyridine 300mg/L NaHCO 3 2000mg/L，MgSO 4 ·7H 2 O0.8873g/L，KCl 0.35g/L，CaCl 2 0.20g/L，FeCl 3 0.03g/L, trace element SL-4 10mL/L.
Microelement SL-4: EDTA0.5g/L FeSO 4 ·7H 2 O 0.2g/L，ZnSO 4 ·7H 2 O 0.001g/L，MnCl 2 ·4H 2 O 0.003g/L，H 3 BO 4 0.03g/L，CoCl 2 ·6H 2 O 0.02g/L，CuCl 2 ·2H 2 O 0.001g/L，NiCl 2 ·6H 2 O 0.002g/L，Na 2 MoO 4 ·2H 2 O 0.003g/L。
Example 1
Preparation of two functional strains and sludge inoculant
(1) Preparation of rhizobium NJUST18 inoculum: rhizobium NJUST18 was inoculated into an inorganic salt medium MSM to which 1g/L pyridine was added, and after shaking culture for 96 hours, the bacterial liquid was centrifuged at 8000 Xg for 10 minutes to obtain bacterial sediment having a dry weight of about 2g as an inoculum.
(2) Culturing nitrified sludge: the sludge is taken from an SBR activated sludge reactor for treating ammonia nitrogen wastewater, and good effect is obtained after more than one year of operation. The sludge was centrifuged at 8000 Xg for 10 minutes to obtain sludge sediment with a dry weight of about 2g as inoculum.
(3) Preparation of Paracoccus denitrificans NJUST53 inoculum: paracoccus denitrificans NJUST53 was inoculated into an inorganic salt medium MSM to which 1g/L glucose was added, and after shaking culture for 96 hours, the bacterial liquid was centrifuged at 8000 Xg for 10 minutes to obtain bacterial sediment having a dry weight of about 2g as an inoculum.
Comparative example 1
Effect of two functional strains and nitrified sludge symbiotic system on degradation and denitrification of pyridine when using traditional oxygen supply mode
Bacterial strains and sludge inoculums were prepared as in example 1, the resulting bacterial cell sediment and sludge sediment were resuspended in sterilized inorganic salt liquid medium, centrifuged, washed three times repeatedly, and bacterial cell and sludge mixtures were resuspended in sterile liquid inorganic salt medium MSM to give bacterial sludge (control OD600 was about 1.7).
Pyridine simulated wastewater using pyridine as the only carbon source and nitrogen source is prepared. The bacterial sludge is added into pyridine simulated wastewater, the inoculation amount is 5%, the hydraulic retention time is 48 hours, and the air compressor is utilized to perform traditional aeration at the maximum aeration pressure of 0.05MPa and the starting times equivalent to MABR at the temperature of 35 ℃. The change in pyridine, total Organic Carbon (TOC) and tristrogen concentration during the culture was monitored.
FIG. 1 shows the effect of a symbiotic system of two functional strains and nitrified sludge on pyridine degradation and denitrification using a conventional oxygen supply mode, (a) shows a change in pyridine concentration, (b) shows a change in trisnitrogen concentration, and (c) shows TN and TOC removal rates. As can be seen from fig. 1, the symbiotic system of the two functional strains and the nitrified sludge cannot realize complete degradation of pyridine within 48 hours, the average removal rate of pyridine is only 68.23%, and the average removal rates of TN and TOC are 17.18% and 63.88%, respectively. In addition, a large amount of pyridine volatilizes in the aeration process to cause secondary pollution. The results show that the symbiotic system of the two functional strains and the nitrified sludge has poor effect of degrading and denitrifying pyridine when the traditional oxygen supply mode is used, and cannot meet the process requirements of pyridine wastewater treatment.
Example 2
MABR startup procedure
The invention combines pyridine degradation strain rhizobium NJUST18 and denitrifying bacteria denitrifying paracoccus NJUST53 with MABR technology. The efficient removal capability of the functional microbial inoculum is combined with the ecological niches (aerobic zone and anoxic zone) of the MABR biological film, so that the process can realize efficient removal of pyridine and nitrogen released by the pyridine.
MABR reactor operation and design parameter conditions: the reactor was a cylindrical MABR reactor made of plexiglas with an effective volume of 2.0L. The membrane component in the MABR reactor is formed by sealing 850 hollow fiber membranes through glue filling, and the total membrane area is up to 0.93m 2 . The hollow fiber membrane is made of Polydimethylsiloxane (PDMS), and has a length of 0.35m, an outer diameter of 1.0mm and an inner diameter of 0.5mm. Air in membraneThe pressure is provided by an air compressor and controlled by an exhaust valve, the aeration pressure ranges from 0.01MPa to 0.05MPa, and the hydraulic retention time is kept at 48 hours. The synthetic wastewater is injected into the bottom of the reactor through a peristaltic pump. The reactor was equipped with a circulation pump to achieve uniform mixing of contaminants in the MABR. In addition, the reactor was incubated in a jacketed circulating water bath with a temperature of 35.+ -. 1 ℃.
As shown in fig. 2, the special device for treating pyridine wastewater mainly comprises: a bioreactor 1, a pyridine wastewater tank 2, an air compressor 8 and a water outlet tank 13; the bioreactor 1 consists of a bottom mud discharging area 5, a water inlet area 4, a membrane aeration component 7 and a top water outlet area 12; the pyridine wastewater tank 1 is communicated with the water inlet area 4 of the bioreactor 1 through the water inlet pump 3, the air compressor 8 is communicated with the membrane aeration assembly 7 of the bioreactor 1 through the ball valve 9 and the pressure gauge 10, the water outlet tank 13 is communicated with the top water outlet area 12 of the bioreactor 1, and in addition, a circulating pump 14 is arranged to form circulation so as to enhance the mixing of the inlet water and the mass transfer efficiency of pollutants, so that the treatment effect of the bioreactor 1 is improved.
As shown in fig. 2, the DO value of the bioreactor 1 is measured at the upper part of the membrane aeration assembly 7 using a dissolved oxygen meter, and the dissolved oxygen of the bioreactor 1 is controlled by adjusting the air compressor 8 and the ball valve 9; the pH of the bioreactor 1 was measured using a pH meter in the upper part of the membrane aeration module 7. The circulation and reflux of the bioreactor 1 is regulated by a reflux pump 14. The measured samples of the bioreactor 1 are the inlet water in the inlet tank 1 and the outlet water in the outlet tank 13.
2. Film hanging process:
(1) Preparation of rhizobium NJUST18 inoculum: rhizobium NJUST18 was inoculated into an inorganic salt medium MSM to which 1g/L pyridine was added, and after shaking culture for 96 hours, the bacterial liquid was centrifuged at 8000 Xg for 10 minutes to obtain bacterial sediment having a dry weight of about 2g as an inoculum. Then the wastewater is injected into an MABR reactor along with pyridine simulated wastewater inflow, continuous flow inflow is carried out after internal circulation is maintained for 3 days, a compact biological film is gradually formed on a fiber film, and finally bacterial inoculum sinking at the bottom of the reactor is discharged out of the system.
(2) After the removal rate of pyridine by the reactor is stable, the nitrified sludge which is domesticated in the embodiment 1 is injected into the reactor, continuous flow water inflow is carried out after internal circulation is maintained for 3 days, a new layer of biological film is gradually covered on the biological film, and finally nitrified sludge inoculums which are sunk at the bottom of the reactor are discharged out of the system.
(3) After the paracoccus denitrificans NJUST53 is subjected to expansion culture according to the method in the embodiment 1, liquid bacteria are centrifuged, residual nutrients are removed by washing, bacterial sediment obtained by centrifugation is used as bacterial inoculum, after the removal rate of pyridine and ammonia nitrogen by the reactor is stable, the bacterial sediment is injected into the reactor along with water inflow, continuous water inflow is carried out after internal circulation is maintained for 3 days, and a new layer of biological film is gradually covered on the biological film. Finally, the bacterial inoculum that settled on the bottom of the reactor was discharged from the system.
The starting state of the bioreactor is judged by taking water samples of the water inlet and the water outlet of the bioreactor every day and performing water quality detection; when the pyridine removal rate of the bioreactor reaches more than 80%, the device is confirmed to be successfully started.
3. Operation of the reactor
Pyridine simulated wastewater is prepared as the inlet water of the MABR reactor, and the initial concentration of pyridine is 300mg/L. In the running process, the hydraulic retention time is 48h, and the temperature is 35+/-1 ℃. The reaction operation is divided into 5 stages, the 1 st stage, the aeration pressure is 0.01MPa, and the pH of the inlet water is 7; 2, the aeration pressure is 0.03MPa, and the pH value of the inlet water is 7; stage 3, aeration pressure is 0.02MPa, and pH of inlet water is 7; stage 4, aeration pressure is 0.02MPa, and pH of inlet water is 8; and 5, the aeration pressure is 0.05MPa, and the pH value of the inlet water is 8.
The performance of MABR in different stages is shown in figures 3-6, when the aeration pressure is 0.01MPa, the removal rate of pyridine is maintained at 87-91%, the ammonia nitrogen concentration of effluent is maintained at 24-28mg/L, and the nitrite nitrogen and nitrate nitrogen concentration is almost zero. When the aeration pressure is increased to 0.03MPa, the pyridine removal rate is 100%, the concentration of ammonia nitrogen and nitrite nitrogen in the effluent is almost zero, and the concentration of nitrate nitrogen is maintained at 11-19mg/L. In order to realize the synchronous nitrification and denitrification process, the aeration pressure is reduced to 0.02Mpa. In the stage, the removal rate of the system to pyridine is still 100%, the nitrate nitrogen concentration is obviously reduced, and the TN removal rate is 83.76 +/-2.1%. To further increase the denitrification rate, the pH of the feed water was increased to 8 to achieve short-cut denitrification. The ammonia nitrogen and nitrate nitrogen concentration in the effluent at this stage is further reduced, TN removal rate is improved to 93.24+/-2.45%, and TOC removal rate is up to 94.88 +/-0.39%. When the aeration pressure is increased to 0.05Mpa, the nitrate nitrogen concentration is significantly increased and maintained at 35-41mg/L in this stage.
The results show that too low aeration pressure makes it difficult to completely remove pyridine, while the remaining pyridine may be toxic to nitrifying bacteria, making it difficult to perform the nitrifying process. Too high aeration pressure will release more dissolved oxygen into the anoxic layer of the biofilm, thereby producing an inhibitory effect on the relevant enzyme activities of denitrifying bacteria in the anoxic layer. In the stage IV, the higher pH value of the inlet water inhibits the activity of NOB, so that the ammonia nitrogen oxidation process is further carried out, and simultaneously, a carbon source is saved for the denitrification process, thereby realizing short-cut nitrification and denitrification.
Mechanism of synchronous short-cut denitrification of pyridine degradation in MABR: pyridine is degraded by pyridine degrading bacteria to release ammonia nitrogen and micromolecular organic matters through diffusing into an aerobic layer of the biological membrane. NH (NH) 4 + N generates NO under the action of ammonia oxidizing bacteria and nitrite oxidizing bacteria with inhibited activity in the aerobic layer of the biofilm 2 - /NO 3 - . Generated NO 2 - /NO 3 - And pyridine/small molecule organic matter generates N under the action of denitrifying bacteria in the anoxic layer 2 And CO 2 。
According to the invention, two functional strains are combined with MABR, and each functional strain lives on each ecological niche, so that the degradation of pyridine and the efficient removal of nitrogen are enhanced. MABR can realize complete degradation of pyridine, and the removal rates of TN and TOC are as high as 93.24% and 94.88%, respectively. The average removal rate of pyridine by the symbiotic system of the two functional strains and the nitrified sludge is only 68.23%, and the average removal rates of TN and TOC are 17.18% and 63.88%, respectively. In addition, the MABR effectively solves the problems of easy volatilization of pyridine, low oxygen utilization rate, difficult denitrification of low carbon ratio wastewater, large occupied area of the traditional aerobic-anoxic process and the like in the traditional aerobic process, and has industrial practicability.
Claims (7)
1. The method for strengthening pyridine degradation and synchronous short-range denitrification by combining functional bacteria with MABR technology is characterized by comprising the following specific steps:
(1) After the rhizobium NJUST18 is subjected to expansion culture, liquid bacteria are centrifuged, residual nutrients are removed by washing, bacterial sediment obtained by centrifugation is used as bacterial inoculum, then the bacterial sediment is injected into an MABR (MABR reactor along with pyridine wastewater inflow, continuous inflow is carried out after internal circulation is maintained for 3-4 days, a compact biological film is gradually formed on a fiber film in the reactor, and finally the bacterial inoculum sinking at the bottom of the reactor is discharged out of the system;
(2) After the pyridine removal rate of the reactor is stable, the nitrified sludge acclimatized by the ammonia nitrogen wastewater is injected into the MABR reactor, continuous flow water inflow is carried out after internal circulation is maintained for 3-4 days, a new layer of biological film is gradually covered on the biological film, and finally, the nitrified sludge sunk at the bottom of the reactor is discharged out of the system;
(3) Centrifuging liquid bacteria after the expansion culture of the paracoccus denitrificans NJUST53, cleaning to remove residual nutrient substances, centrifuging again to obtain bacterial sediment serving as bacterial inoculum, injecting the bacterial sediment into the MABR (MABR reactor along with the inlet water after the removal rate of pyridine and ammonia nitrogen by the reactor is stable, carrying out continuous flow inlet after maintaining the internal circulation for 3-4 d, gradually covering a layer of new biological film on the biological film, and finally discharging the bacterial inoculum sinking at the bottom of the reactor out of the system;
(4) The aeration pressure and the pH value of the inlet water are respectively controlled at 0.02+/-0.005 MPa and 8.0-8.2, and synchronous short-range denitrification of pyridine degradation is realized by using MABR.
2. The method of claim 1, wherein in step (1), the rhizobium strain NJUST18 has been deposited at the chinese collection at 3 months and 28 days 2013 with a deposit number of cctccc NO: m2013110.
3. The method according to claim 1, wherein in the step (3), the paracoccus denitrificans NJUST53 is preserved in the China center for type culture collection (CCTCC No.) at a date of 2022, 03 and 02: m2022178.
4. The method according to claim 1, wherein in the step (1), the specific method for the enlarged culture of rhizobium japonicum NJUST18 is as follows: rhizobium NJUST18 is inoculated into an inorganic salt culture medium MSM added with 1g/L pyridine, and shake cultivation is performed for more than 96 hours.
5. The method according to claim 1, wherein in the step (3), the specific method for the expansion culture of Paracoccus denitrificans NJUST53 is as follows: paracoccus denitrificans NJUST53 was inoculated into an inorganic salt medium MSM to which 1g/L glucose was added, and shake-cultured for 96 hours or more.
6. The method according to claim 1, wherein the composition of the inorganic salt medium MSM is: na (Na) 2 HPO 4 ·2H 2 O 3.5g/L，KH 2 PO 4 1g/L，(NH4) 2 SO 4 500mg/L，MgCl 2 ·6H 2 O 100mg/L，Ca(NO 3 ) 2 ·4H 2 50mg/L of O and 1.0ml/L of trace element SL-4; wherein the composition of the trace elements SL-4 is as follows: EDTA0.5g/L, feSO 4 ·7H 2 O 0.2g/L，ZnSO 4 ·7H 2 O 0.001g/L，MnCl 2 ·4H 2 O 0.003g/L，H 3 BO 4 0.03g/L，CoCl 2 ·6H 2 O 0.02g/L，CuCl 2 ·2H 2 O 0.001g/L，NiCl 2 ·6H 2 O 0.002g/L，Na 2 MoO 4 ·2H 2 O0.003g/L。
7. The method according to claim 1, wherein in the step (1), (2) or (3), the centrifugation speed is 8000 rpm, the centrifugation time is 10min, and the washing liquid is phosphate buffer solution.
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| CN116395854B (en) * | 2023-05-25 | 2024-02-06 | 广东工业大学 | Device and method for self-induced shortcut nitrification-denitrification of waste water anaerobic digestion liquid |
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