CN108341572B - Method for realizing sludge recessive growth reduction by Fenton oxidation coupled microorganism iron reduction - Google Patents

Method for realizing sludge recessive growth reduction by Fenton oxidation coupled microorganism iron reduction Download PDF

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CN108341572B
CN108341572B CN201810108673.7A CN201810108673A CN108341572B CN 108341572 B CN108341572 B CN 108341572B CN 201810108673 A CN201810108673 A CN 201810108673A CN 108341572 B CN108341572 B CN 108341572B
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CN108341572A (en
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薛罡
陈红
钱雅洁
李响
张文启
刘振鸿
孟程程
李珂
徐先宝
王静
张禾
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Shanghai Senxi Environmental Engineering Co ltd
Donghua University
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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
    • C02F11/00—Treatment of sludge; Devices therefor
    • C02F11/02—Biological treatment
    • C02F11/04—Anaerobic treatment; Production of methane by such processes
    • C—CHEMISTRY; METALLURGY
    • C02—TREATMENT OF WATER, WASTE WATER, SEWAGE, OR SLUDGE
    • C02F—TREATMENT OF WATER, WASTE WATER, SEWAGE, OR SLUDGE
    • C02F11/00—Treatment of sludge; Devices therefor
    • C02F11/06—Treatment of sludge; Devices therefor by oxidation
    • C—CHEMISTRY; METALLURGY
    • C02—TREATMENT OF WATER, WASTE WATER, SEWAGE, OR SLUDGE
    • C02F—TREATMENT OF WATER, WASTE WATER, SEWAGE, OR SLUDGE
    • C02F11/00—Treatment of sludge; Devices therefor
    • C02F11/12—Treatment of sludge; Devices therefor by de-watering, drying or thickening
    • C02F11/121—Treatment of sludge; Devices therefor by de-watering, drying or thickening by mechanical de-watering
    • C02F11/122—Treatment of sludge; Devices therefor by de-watering, drying or thickening by mechanical de-watering using filter presses
    • C—CHEMISTRY; METALLURGY
    • C02—TREATMENT OF WATER, WASTE WATER, SEWAGE, OR SLUDGE
    • C02F—TREATMENT OF WATER, WASTE WATER, SEWAGE, OR SLUDGE
    • C02F11/00—Treatment of sludge; Devices therefor
    • C02F11/12—Treatment of sludge; Devices therefor by de-watering, drying or thickening
    • C02F11/14—Treatment of sludge; Devices therefor by de-watering, drying or thickening with addition of chemical agents
    • C—CHEMISTRY; METALLURGY
    • C02—TREATMENT OF WATER, WASTE WATER, SEWAGE, OR SLUDGE
    • C02F—TREATMENT OF WATER, WASTE WATER, SEWAGE, OR SLUDGE
    • C02F3/00—Biological treatment of water, waste water, or sewage
    • C02F3/30—Aerobic and anaerobic processes
    • C—CHEMISTRY; METALLURGY
    • C02—TREATMENT OF WATER, WASTE WATER, SEWAGE, OR SLUDGE
    • C02F—TREATMENT OF WATER, WASTE WATER, SEWAGE, OR SLUDGE
    • C02F2303/00—Specific treatment goals
    • C02F2303/06—Sludge reduction, e.g. by lysis

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  • Life Sciences & Earth Sciences (AREA)
  • Chemical & Material Sciences (AREA)
  • Organic Chemistry (AREA)
  • Environmental & Geological Engineering (AREA)
  • Water Supply & Treatment (AREA)
  • Hydrology & Water Resources (AREA)
  • Chemical Kinetics & Catalysis (AREA)
  • General Chemical & Material Sciences (AREA)
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  • Oil, Petroleum & Natural Gas (AREA)
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  • Treatment Of Water By Oxidation Or Reduction (AREA)
  • Treatment Of Sludge (AREA)
  • Activated Sludge Processes (AREA)

Abstract

The invention discloses a method for realizing recessive growth and decrement of sludge by utilizing Fenton oxidation coupled microorganism iron reduction, after sewage is subjected to biochemical reaction of activated sludge, sludge-water mixed liquor is statically precipitated in a secondary precipitation tank, part of sludge flows back to a biochemical reaction system, and the rest sludge is discharged into a sludge concentration tank for concentration treatment; the sludge in the concentration tank is conditioned, dehydrated, transported and disposed, and the part of the sludge is discharged into a microorganism iron reduction tank to realize sludge hydrolysis and Fe3+Reduction of (2); discharging the sludge into a sludge Fenton reaction tank after passing through a microbial iron reduction tank, and starting a Fenton reaction to perform cell breaking treatment on the sludge; transferring the sludge cell-breaking liquid to a regulating tank, and further reducing the endogenous consumption of the sludge; and returning the sludge cell-breaking liquid in the regulating tank to the biochemical reaction tank. The invention can realize sludge reduction in the sewage treatment system and enhance the biochemical treatment effect of the wastewater, has simple operation and lower cost, and provides a feasible method for high-efficiency reduction of excess sludge and improvement of the biochemical treatment effect of the wastewater.

Description

Method for realizing sludge recessive growth reduction by Fenton oxidation coupled microorganism iron reduction
Technical Field
The invention belongs to the technical field of environmental protection, and particularly relates to a method for realizing sludge recessive growth reduction by Fenton oxidation coupled with microbial iron reduction.
Background
In recent years, the problem of disposal of excess sludge has become an environmental problem which is urgently solved all over the world, and since sewage treatment is mainly carried out by an activated sludge method, a large amount of excess sludge rich in organic matters is generated in the sewage treatment process. According to statistics, the dry sludge produced in China in 2013 weighs about 6250000 tons, and has an annual growth rate of 13% from 2007 to 2013 (Water Research, 2015, 78: 60-73), and the sludge which is not properly treated and disposed can cause serious harm to the environment and human health. At present, the method based on sludge treatment mainly focuses on four aspects of reduction, harmlessness, stabilization and resource utilization. Because the residual sludge is rich in organic matters, in recent years, research has been carried out on a recessive growth sludge reduction technology, namely a growth mode that microorganisms synthesize microorganism organisms again by using substrates formed by cell hydrolysis, wherein the substrates used for recessive growth are products of cell breakage. The process of breaking the sludge product and returning the sludge product to the biological treatment system and utilizing the sludge product by the microorganisms is theoretically analyzed, and certain sludge reduction effect is necessarily realized.
In order to achieve the aim of recessive growth and decrement of the sludge, the key point is to realize effective cell breaking of the sludge, strengthen the hydrolysis of the sludge by physical, chemical or biological means, destroy the cell structure of microorganisms in the sludge, break zoogloea flocs of the sludge, release solid organic matters in the microbial thalli into a liquid phase to become dissolved organic matters, and the part of the organic matters can be used as a substrate for recycling the sludge in a sewage treatment system. As a key of the recessive growth of sludge, namely sludge cell breaking, currently, cell breaking technologies researched comprise an ultrasonic method, a mechanical shearing method, a high pressure method, a heating method, ozone oxidation, alkali addition for breaking, enzyme preparation addition and the like, but the problems of high cost, high energy consumption, poor reduction effect and the like are limited, and the method is rarely applied at present.
Disclosure of Invention
The invention aims to solve the problems that: how to utilize fenton oxidation coupling microorganism iron reduction to realize the recessive growth decrement of sludge and improve the treatment effect of waste water simultaneously.
In order to solve the problems, the invention adopts the following technical scheme:
a method for realizing sludge recessive growth reduction by Fenton oxidation coupled microorganism iron reduction is characterized by comprising the following steps:
step 1): after the sewage is subjected to biochemical reaction by activated sludge, the sludge-water mixed liquor is statically precipitated in a secondary precipitation tank, part of sludge flows back to a biochemical reaction system, and the rest sludge is discharged into a sludge concentration tank for concentration treatment;
step 2): the sludge in the concentration tank is treated by conditioning and dewatering, transported outside and discharged into a microorganism iron reduction tank, the microorganisms are kept under anaerobic conditions, and stirring reaction is carried out to realize sludge hydrolysis and Fe3+Reduction of (2);
step 3): discharging the sludge into a sludge Fenton reaction tank after passing through a microorganism iron reduction tank, adding acid to adjust the pH value to be acidic, and adding Fe2+And H2O2Stirring, and starting a Fenton reaction to perform cell breaking treatment on the sludge;
step 4): after the Fenton reaction, transferring the sludge cell-breaking liquid to an adjusting tank, adding alkali to adjust the pH value, and aerating to ensure that Fe in the Fenton reaction process2+Conversion to Fe3+The sludge realizes further endogenous consumption reduction;
step 5): and returning the sludge cell-breaking liquid in the regulating tank to the biochemical reaction tank to be used as a sludge growth carbon source to be utilized by activated sludge, so as to realize the recessive growth decrement of the sludge.
Preferably, the proportion of the sludge returned to the biochemical reaction system in the step 1) is 50-100%, the rest sludge is subjected to gravity concentration treatment for 12-20h, the concentration of the concentrated sludge is 15-25g/L, 50-85% of the sludge after the concentration treatment is pumped into a microorganism iron reduction pool, and the rest sludge is conditioned, dehydrated and transported for disposal.
Preferably, the microorganism iron reduction pool in the step 2) adopts a slow mechanical stirring or bottom stirring mode to maintain sludge mixing without precipitation, the stirring speed is 20-60rpm/min, the dissolved oxygen concentration is less than 0.5mg/L, and the anaerobic reaction lasts for 1-4 d.
Preferably, the pH value of the sludge Fenton reaction tank in the step 3) is adjusted to 3-5 by adopting sulfuric acid or hydrochloric acid, and Fe is added2+FeCl can be used2Or FeSO4，Fe2+The addition amount of (A) is 0.05-0.2kg/(kg dry sludge), H2O2The adding amount of the catalyst is 0.3-3mol/(kg dry sludge), the mechanical stirring speed is 60-150rpm/min, and the Fenton reaction time is 0.5-5 h.
Preferably, the alkali added into the sludge cell-breaking liquid in the regulating tank in the step 4) is NaOH or Ca (OH)2Adjusting the pH value to 6-8; aerating to make the dissolved oxygen concentration be 0.5-3.0 mg/L, and aerating for 0.5-3 h.
Preferably, the sludge cell-breaking liquid in the step 5) enters from the front end of the water inlet of the biochemical pool, and participates in biochemical reaction after being mixed with sewage, so that recessive growth and reduction of sludge are realized, and the biochemical treatment effect of wastewater is improved.
The invention provides a method for realizing excess sludge reduction, which comprises the steps of carrying out cell breaking treatment on excess activated sludge through Fenton reaction, releasing an intracellular organic carbon source, coupling endogenous consumption reduction of the sludge, returning sludge cell breaking liquid to a sewage biochemical treatment system again to participate in biochemical reaction of the activated sludge, and adding Fe3+Is beneficial to the metabolism of organisms and can be assisted by chemical phosphorus removal. The secondary sedimentation tank is introduced by Fenton cell-breaking liquid, and discharged sludgeContaining Fe3+Coupling a microorganism iron reduction pool in front of the Fenton reaction pool to reduce Fe3+Reduction to Fe2+Is beneficial to reducing Fe in the subsequent Fenton reaction tank2+The usage amount of the microbial iron reduction pool and the hydrolysis of the residual sludge in the microbial iron reduction pool are also beneficial to the cell breaking efficiency of the sludge in the Fenton reaction pool, thereby achieving the purposes of reducing the usage amount of medicaments and improving the sludge reduction effect.
Compared with the prior art, the invention has the following beneficial effects:
(1) the method is coupled with Fenton treatment of sludge to realize sludge cell breaking, further aeration is performed after cell breaking to realize endogenous consumption reduction of the sludge, and reduction of the consumption of Fenton reagents is realized by coupling with reduction of microorganism iron, so that the sludge reduction effect is improved, and the sludge reduction can be realized by 35-60%;
(2) the Fenton reaction used in the method contains iron ions, and the iron ions enter the biochemical reaction system along with the sludge cell-breaking liquid, so that the growth of microorganisms in the biochemical reaction system is facilitated, the phosphorus removal is enhanced, the flocculation property and the precipitation property of the sludge are improved, and the high efficiency and the stability of a sewage biochemical system are realized;
(3) the method can realize the reduction of the sludge in the sewage treatment system, and has the advantages of simple and easy technology, lower cost and good reduction effect.
Drawings
FIG. 1 is a process diagram of a method for realizing sludge recessive growth reduction by Fenton oxidation coupled with microbial iron reduction provided by the invention.
Detailed Description
In order to make the invention more comprehensible, preferred embodiments are described in detail below with reference to the accompanying drawings.
Example 1
A method for realizing sludge recessive growth reduction by Fenton oxidation coupled microorganism iron reduction comprises the following steps:
(1) a certain printing and dyeing wastewater treatment plant adopts an anaerobic-anoxic-aerobic (AAO) biochemical treatment process to remove organic matters, nutrient substances and nitrogen and phosphorus in the wastewater. Two groups of process reactors which are the same as the printing and dyeing wastewater treatment plant are constructed in a laboratory, activated sludge of the wastewater treatment plant with the same concentration is inoculated, the COD concentration of biochemical reaction inlet water is 550mg/L, the ammonia nitrogen concentration is 45-60mg/L, the total nitrogen concentration is 55-70mg/L, the total phosphorus concentration of the inlet water is 5-10mg/L, after AAO biochemical treatment and stable operation, the COD concentration of outlet water of the two groups of reactors is 110-150mg/L, the ammonia nitrogen concentration is 5-8mg/L, the total nitrogen concentration is 18-25mg/L, and the total phosphorus concentration is 1.2-2.0 mg/L.
(2) As shown in fig. 1, in one of the reactors, sewage enters a secondary sedimentation tank for sludge-water separation after biochemical reaction, the ratio of returned sludge is 80%, the rest part enters a sludge concentration tank, gravity concentration treatment is carried out for 12 hours, the concentration of the concentrated sludge is 16g/L, 50% of the concentrated sludge is discharged into a microorganism anaerobic iron reduction reaction tank, and the other 50% of the concentrated sludge is subjected to plate-frame pressure filtration after lime conditioning; in a microorganism anaerobic iron reduction pool, a mechanical stirring mode is adopted, the stirring speed is 20rpm/min, the dissolved oxygen concentration is less than 0.5mg/L, and the reaction time is 1.5 d; adding sulfuric acid to adjust the pH value to 4 in a sludge Fenton reaction tank, adding FeCl2Of Fe2+The addition amount of (2) is 0.05kg/(kg dry sludge), H2O2The adding amount of the catalyst is 0.6mol/(kg dry sludge), the mechanical stirring speed is 80rpm/min, and the Fenton reaction time is 1 h; discharging the sludge cell-breaking liquid after the Fenton reaction to an adjusting tank, adding NaOH, and adjusting the pH value to 6-8; aerating to ensure that the concentration of dissolved oxygen is 1mg/L and the aeration time is 1 h; and pumping the sludge breaking liquid in the regulating tank to the water inlet front end of the biochemical tank, mixing the sludge breaking liquid with the sewage, and participating in biochemical reaction.
(3) In the other group of reactors, sewage enters a secondary sedimentation tank for sludge-water separation after biochemical reaction, the ratio of returned sludge is 80 percent, the rest part of sludge is completely discharged into a sludge concentration tank, and the sludge in the concentration tank is conditioned by lime and is subjected to plate-frame filter pressing.
(4) After 15 days of operation, the yield of the sludge is reduced by 42% compared with that of the other group by adopting an experimental group for oxidizing the sludge by Fenton; the Fenton oxidation sludge experimental group further improves the treatment effect, the COD concentration of the effluent is 60-80mg/L, the ammonia nitrogen concentration is 5-6mg/L, the total nitrogen concentration is 10-12mg/L, and the total phosphorus concentration is 0.1-0.3 mg/L.
Example 2
A method for realizing sludge recessive growth reduction by coupling Fenton reaction with microbial iron reduction comprises the following steps:
(1) the inversion A2O process is adopted for removing organic matters, nutrient substances and nitrogen and phosphorus in certain domestic sewage. Two groups of process reactors which are the same as the printing and dyeing wastewater treatment plant are constructed in a laboratory, activated sludge of the wastewater treatment plant with the same concentration is inoculated, the COD concentration of biochemical reaction inlet water is 350-420mg/L, the ammonia nitrogen concentration is 35-50mg/L, the total nitrogen concentration is 45-55mg/L, the concentration of total phosphorus of the inlet water is 8-13mg/L, after the biochemical treatment by the inverted A2O process, the operation is stable, the COD concentration of the outlet water of the two groups of reactors is 65-85mg/L, the ammonia nitrogen concentration is 5-8mg/L, the total nitrogen concentration is 15-20mg/L, and the total phosphorus concentration is 1.0-1.5 mg/L.
(2) As shown in figure 1, in one group of reactors, after biochemical reaction, sewage enters a secondary sedimentation tank for sludge-water separation, the ratio of returned sludge is 60%, the rest part enters a sludge concentration tank, gravity concentration treatment is carried out for 15 hours, the concentration of the concentrated sludge is 18g/L, 70% of the concentrated sludge is discharged into a microorganism anaerobic iron reduction reaction tank, and the other 30% of the concentrated sludge is conditioned by lime and is subjected to plate-frame filter pressing; in a microorganism anaerobic iron reduction pool, a mechanical stirring mode is adopted, the stirring speed is 25rpm/min, the dissolved oxygen concentration is less than 0.5mg/L, and the reaction time is 2.0 d; adding hydrochloric acid into a sludge Fenton reaction tank to adjust the pH value to 3.5, and adding FeCl2Of Fe2+The addition amount of (2) is 0.15kg/(kg dry sludge), H2O2The adding amount of the catalyst is 1.2mol/kg (dry sludge), the mechanical stirring speed is 90rpm/min, and the Fenton reaction time is 2 hours; discharging the sludge cell-breaking liquid after the Fenton reaction to a regulating tank, and adding Ca (OH)2Adjusting the pH value to 7.5; aerating to make the dissolved oxygen concentration be about 1.0mg/L, and the aeration time be 2 h; and pumping the sludge breaking liquid in the regulating tank to the water inlet front end of the biochemical tank, mixing the sludge breaking liquid with the sewage, and participating in biochemical reaction.
(3) In the other group of reactors, sewage enters a secondary sedimentation tank for sludge-water separation after biochemical reaction, the reflux sludge ratio is 60 percent, the rest part of sludge is completely discharged into a sludge concentration tank, and the sludge in the concentration tank is conditioned by lime and is subjected to plate-frame filter pressing.
(4) After 30 days of operation, the yield of the sludge is reduced by 50% compared with that of the other group by adopting an experimental group for oxidizing the sludge by Fenton; the Fenton oxidation sludge experimental group further improves the treatment effect, the COD concentration of the effluent is 35-45mg/L, the ammonia nitrogen concentration is 3-5mg/L, the total nitrogen concentration is 6-12mg/L, and the total phosphorus concentration is 0.1-0.2 mg/L.

Claims (4)

1. A method for realizing sludge recessive growth reduction by Fenton oxidation coupled microorganism iron reduction is characterized by comprising the following steps:
step 1): after the sewage is subjected to biochemical reaction by activated sludge, the sludge-water mixed liquor is statically precipitated in a secondary precipitation tank, part of sludge flows back to a biochemical reaction system, and the rest sludge is discharged into a sludge concentration tank for concentration treatment;
step 2): the sludge in the concentration tank is treated by conditioning and dewatering, transported outside and discharged into a microorganism iron reduction tank, the microorganisms are kept under anaerobic conditions, and stirring reaction is carried out to realize sludge hydrolysis and Fe3+Reduction of (2);
step 3): discharging the sludge into a sludge Fenton reaction tank after passing through a microorganism iron reduction tank, adding acid to adjust the pH value to be acidic, and adding Fe2+And H2O2Stirring, and starting a Fenton reaction to perform cell breaking treatment on the sludge; the pH value of the sludge Fenton reaction tank is adjusted to 3-5 by adopting sulfuric acid or hydrochloric acid, and added Fe2+Using FeCl2Or FeSO4，Fe2+The addition amount of (A) is 0.05-0.2kg/kg dry sludge, H2O2The adding amount of the sludge is 0.3-3mol/kg of dry sludge, the mechanical stirring speed is 60-150rpm, and the Fenton reaction time is 0.5-5 h;
step 4): after the Fenton reaction, transferring the sludge cell-breaking liquid to a regulating tank, adding alkali to regulate the pH value, and aerating to ensure that Fe in the Fenton reaction process2+Conversion to Fe3+The sludge realizes further endogenous consumption reduction; the alkali added into the sludge cell-breaking liquid in the regulating tank is NaOH or Ca (OH)2Adjusting the pH value to 6-8; aerating to make the concentration of dissolved oxygen be 0.5-3.0 mg/L, and the aeration time be 0.5-3 h;
step 5): and returning the sludge cell-breaking liquid in the regulating tank to the biochemical reaction tank to be used as a sludge growth carbon source to be utilized by activated sludge, so as to realize the recessive growth decrement of the sludge.
2. The method for realizing the recessive sludge growth reduction by utilizing Fenton oxidation coupled microorganism iron reduction according to claim 1, wherein the proportion of the sludge reflowing to the biochemical reaction system in the step 1) is 50-80%, the rest sludge is subjected to gravity concentration treatment for 12-20h, the concentration of the concentrated sludge is 15-25g/L, 50-85% of the concentrated sludge is pumped into a microorganism iron reduction pool, and the rest sludge is conditioned, dehydrated and transported for disposal.
3. The method for realizing sludge recessive growth reduction by utilizing Fenton oxidation coupled microorganism iron reduction according to claim 1, wherein the microorganism iron reduction pool in the step 2) adopts a slow mechanical stirring mode or a bottom stirring mode to maintain sludge mixing without precipitation, the stirring speed is 20-60rpm, the dissolved oxygen concentration is less than 0.5mg/L, and the anaerobic reaction lasts for 1-4 d.
4. The method for realizing the recessive growth and decrement of sludge by utilizing the Fenton oxidation coupled microorganism iron reduction as claimed in claim 1, wherein the sludge cell-breaking liquid in the step 5) enters from the front end of the influent water of the biochemical tank, and participates in biochemical reaction after being mixed with the sewage, so that the recessive growth and decrement of sludge are realized, and the biochemical treatment effect of the wastewater is improved.
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Citations (6)

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Publication number Priority date Publication date Assignee Title
WO2009101455A1 (en) * 2008-02-11 2009-08-20 Pantelis Xynogalas Physicochemical method of processing liquid and semisolid wastes of olive mills using ozone (o3)
CN103755096A (en) * 2014-01-17 2014-04-30 上海交通大学 Coupled Fenton oxidation and anaerobic digestion reactor for treating surplus sludge
CN105366899A (en) * 2015-12-10 2016-03-02 东华大学 Ozone-anaerobic iron reduction combined Fenton oxidation technology for sludge reduction
CN105417869A (en) * 2015-12-10 2016-03-23 东华大学 Fenton oxidation-biological combination treatment technology capable of achieving ozone-anaerobic iron reduction and sludge reduction
CN107140804A (en) * 2017-03-06 2017-09-08 天津壹新环保工程有限公司 Fenton method for sludge treatment and device that a kind of molysite is recycled
CN206553372U (en) * 2017-03-06 2017-10-13 天津壹新环保工程有限公司 The Fenton sludge treatment equipment that a kind of molysite is recycled

Patent Citations (6)

* Cited by examiner, † Cited by third party
Publication number Priority date Publication date Assignee Title
WO2009101455A1 (en) * 2008-02-11 2009-08-20 Pantelis Xynogalas Physicochemical method of processing liquid and semisolid wastes of olive mills using ozone (o3)
CN103755096A (en) * 2014-01-17 2014-04-30 上海交通大学 Coupled Fenton oxidation and anaerobic digestion reactor for treating surplus sludge
CN105366899A (en) * 2015-12-10 2016-03-02 东华大学 Ozone-anaerobic iron reduction combined Fenton oxidation technology for sludge reduction
CN105417869A (en) * 2015-12-10 2016-03-23 东华大学 Fenton oxidation-biological combination treatment technology capable of achieving ozone-anaerobic iron reduction and sludge reduction
CN107140804A (en) * 2017-03-06 2017-09-08 天津壹新环保工程有限公司 Fenton method for sludge treatment and device that a kind of molysite is recycled
CN206553372U (en) * 2017-03-06 2017-10-13 天津壹新环保工程有限公司 The Fenton sludge treatment equipment that a kind of molysite is recycled

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