991 resultados para NH4


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CODNH4+-N 86.77.6 mg/L35.47%59.28%CODNH4+-N 2.420.139kg/(m3d)CODNH4+-N 85.058.4mg/L25.1%28.7%GB 8978-199638%49% 1,2-1,2-1,2-COD 1000mg/L COD 20%16%1,2- Currently, Chinas oil refining industry is developing rapidly and has become the second largest all over the world. The oil refining industry is one of the major pollution industries in our country. The pilot scale study and engineering application research were conducted aiming at the problems in refining wastewater such as poor treatment stability and water quality, poor anti-shock capacity and expensive running cost, etc., so as to provide theoretical references and technological supports for the engineering application and popularization of microbial preparation in wastewater treatment. Also, the response mechanism of functional microbe under shock of different phenol concentrations, which is the main pollutants in refinery wastewater, was studied. Based on this result, functional microbe activation accelerator was developed, and the regulation effect of functional microbe biological index under phenol shocking were studied, in order to provide theoretical basis and technological support for regulation of toxic shocking of wastewater biological treatment. The result of pilot scale research indicated: for treatment of refinery wastewater in bioaugmention treatment system of microbial preparation, the COD and NH4+-N average value of effluent was 86.7 and 7.6 mg/L, Comparing with normal biological treatment system, the average removal rates of COD, NH4+-N increased 35.47%,59.28% separately by bioaugmention treatment system, which showed better anti-shocking capacity, the volumetric load r of COD and NH4+-N reached 2.42 kg/(m3d) and 0.139 kg/(m3d), respectively. The research on engineering application of refinery wastewater bioaugmentation treatment by microbial preparation indicated:the average concentrations of effluent COD and NH4+-N in the bioaugmentation treatment system were 85.05 and 8.4mg/L, which increased by 25.1% and 28.7% comparing with normal biological treatment system of refinery wastewater, And the effluent quality meets the first grade of discharging standard of National Integrated Wastewater Discharge Standard GB 8978-1996. The economic analysis of technology indicated: the demonstration project of bioaugmentation treatment of refinery wastewater by microbial preparation decreased by 38% in construction cost and 49% in running cost. This technology has economic benefits. The response mechanism of functional microbe under phenol shock indicated: biological index such as the biomass concentration, dehydrogenase and 1,2-dioxygenase had different responses under phenol shocking of different concentrations. The response sensitivity of different biological index under phenol shocking of different concentrations is: dehydogenase activity biomass 1,2-dioxygenase activity, and high correlation of 1,2-dioxygenase and COD degradation percentage is achieved, thus 1,2-dioxygenase could be used to reflect the degradation situation of pollutants. So, 1,2-dioxygenase is the keypoint of regulation. The anti-shock activation accelerator of phenol degradation functional microbe was primarily developed. The results indicated: the activation accelerator could regulate the degradation effect of toxic substance-phenol by functional microbe effectively. For the functional microbe treatment system under phenol shocking of 1000mg/L, the COD degradation rate increased by 20% and the degradation time reduced by more than 16% under regulation of activation accelerator. The regulation effects of biological index are: 1,2-dioxygenase biomass dehydrogenase. In this way, the response mechanism of functional microbe under toxic shocking is verified. The result indicated: the augmented microbial preparation treatment of refinery wastewater is applicable. It has many technical and economical advantages. The research results of responses mechanism of wastewater treatment system on toxic pollutants would offer a new idea for regulation of anti-shock.

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1ERIC-PCRFPNFCBF14FEm20%76 2 3g/L 31.0g/L10.0g/L1.0g/L1.1g/L0.55g/LpH7.532125mL250 mL20 h1.125 g/L0.1 g/L4 h 4FPNF10FCBFNaF14 FEm 52%3500 mg/L24 hCOD36.8%97%SBRSBRCOD27.1%SBRSBRSBRSBRSBR Along with the development of industries, many recalcitrant organic chemicals have been discharged into natural environments together with wastewaters and can exist in waters, soil and sediments for a long time without degradation. These haz-ardous substances, their byporducts and metabolizabilities can be highly toxic, mu-tagenic and carcinogenic, thereby threatening animals, plants and human health through food chain. Consequently the removal of these compounds is of significant interest in the area of wastewater treatment. In this dissertation, the phenol, hydro-quinone, chlorobenzene and hexadecane treated as the model pollutants, the func-tional microorganism agent was used as the starting strains, they treated with ultra-violet light, and then the mutant strains with high degradation ability were screened out and identified primarily, the relationship between these stains were studied, the medium composition and fermentation conditions were optimized, the degradation ability of the fermented production was tested. The literature survey indicates that the study of the microorganism agent is far from complete and more information is re-quired on following problems. 1, Because of the complexity of relationship in mixed fermentation and the complicated factors, the study is hardly to process.2, There is a lack of information on the quality control of the producing process .3, And there is a lack of information on the stability about the microorganism agent. In this dissertation, the main results of the present study could be summarized as follows: (1)The degenerate starting strains were treated with the ultraviolet light, and six mutant strains with high biodegradation ability were screened out by using the me-dium with selective pressure of model pollutants. The mutant strains had great changes in colonialmorphology and ERIC-PCR fingerprinting. And the mutant strains got obvious advantages over the starting strains in degradation ability and over 20% improvement of removal rates was achieved for FPNFCBF14 and FEm. The de-gradation ability of the mutant strains was stable after seven generations. After that, the mutant strains were primarily identified as bacillus respectively. (2) The relationship between these mutant strains was studied. By the compari-son of antibiosis effect, biomass and consumption of substrate, the relationships were neutralism and they could be mixed fermented. (3) The optimized cultivation conditions were as follows: glucose 31.0 g/L, corn power 10 g/L, K2HPO4 1.0 g/L, (NH4)2SO4 1.1 g/L, MgSO4 0.55 g/L, initial pH7.5, temperature 32, working volume 125 mL/250 mL, and cultivation time 20h (con-sidering the time effect on degradation ability), adding pollutants phenol (1.125 g/L) and hydroquinone (0.1 g/L) into the broth at 4 h after cultivation. (4) Based on the above optimum condition, the batch fermentation was per-formed with strains FPN, F10, FCB, FNa, F14 and FEm in shake flask. The batch fermentation kinetics was studied based on the experimental data. Two kinetic models were constructed which could reflect the regularity of growth and substrate consump-tion in the process of batch fermentation. (5) The co-operation of functional microorganism agent and activated sludge could raise biodegradation of system by adding some microorganism agent and 3500 mg/L fresh activated sludge. Bioaugumentation by the addition of high effective deg-radation culture enhanced the treatment effect of SBR system and the COD removal rate was increased by 20%-36.8%. Its biodegradation matched first-order dynamical reaction equation, and the reaction equation was ln0.2327.391ct=+. The micro-organism agent had the effect of optimization to activated sludge micro-ecosystem. The SBR system adding 2% microorganism agent, the average COD removal rate of that was increased by 27.1% and stronger anti-shock ability to load and toxicant were achieved (compared with SBR system just adding activated sludge). Especially the load-shock has barely effect to the SBR system adding microorganism agent. After the load and toxicant shock, the SBR system just adding activated sludge couldnt come back to original level and the activated sludge micro-ecosystem was frustrated. The applying of microorganism agent increased biological activity and systems re-sistance ability to load shock and toxicant shock.

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8,000~12,0003,500 tSS1.2105 tCOD1.8105 tBOD7104 t SBBRBAF COD3,000 mg/LCOD200 mg/LCOD3,000 mg/LCOD200 mg/L COD2,000~2,500 mg/LNH4+-N130~146 mg/LCODNH4+-NSBBR93.8%~96.6%14.5%~55.9%SBR88.8%~94.9%13%~50.7%SBBRSBRSBBR0.05 kgVSS/kgCODSBR0.57 kgVSS/kgCOD8.8%SBBR3SBR9SBBRSBR SBBRBAFCOD 801~2,834 mg/LNH4+-N 87~203 mg/LCOD80 mg/LNH4+-N10 mg/L 69COD6~8 hCOD200 mg/L8~10 hCOD200 mg/LSBBRCODNH4+-NSBBRCOD53 mg/L74 mg/L84 GB8976-1996 As a labour-intensive industry, tanning has created large amount of working opportunities as well as caused severe contamination to environment. And it is one of the highest water-consuming and polluting industry, only second to manufacturing. At present time, Chinese leather industry emits wastewater about 80,000,000~120,000,000 t annually, which contains chromium about 3,500 t, SS 1.2105 t, COD 1.8105 t, BOD 7104 t and ambient riverhead has been polluted greatly. Based on the research of anaerobic acidification and comparison of SBBR and SBR, biotreatment process (HomogenizationSBBRBAF) had been established to amend the disadvantages of traditional sewage treatment such as too much sludge, high cost of advanced treatment and NH4+-N can not reach the emission standard. Research on the bioaugmentation was also been carried out. Researches showed, when COD of influent was beyond 3,000 mg/L, anaerobic acidification could resist strong impact, thus COD of effluent was less than 200 mg/L; when COD of influent was less than 3,000 mg/L, only throughout aerobic sewage treatment could COD of effluent beless than 200 mg/L. False residence tiome of anaerobic acidification would lead to the higher effluent concentration of sulfide and disintegration of aerobic activated sludge. Researches showed SBBR worked a better than SBR: when influent between 2,000 and 2,500 mg/L, NH4+-N between 130 mg/L and 146 mg/L, COD, NH4+-N removal rate of SBBR was 93.3%~96.6%, 14.5%~55.9% respectively while COD, NH4+-N removal rate of SBR was 88.8%~94.9%, 13%~50.7% respectively. Sludge growth rate of SBBR was 8.8% of that of 0.05 kgVSS/kgCOD. Besides, SBBR could recovered after 3 operating periods while SBR worked no better after 9 operating periods.Therefore, SBBR excelled SBR. Researches showed, effluent quantity of tannery wastewater treatment process (HomogenizationSBBRBAF) was stable. When COD of influent was between 801 and 2,834 mg/L, NH4+-N was between 87 mg/L and 203 mg/L, COD of effluent was less than 80 mg/L, NH4+-N was less than 10 mg/L, which achieved the standard of reuse. This biotreatment was featured in low cost, easy and flexible management, less sludge, no inverse sludge system. Besides, this technique required no chemical, which could lower the cost and avoid secondary pollution. Great resistant of impact due to two membranes and was suitable for tannery wastewater which was featured by fluctuation of influent quality and quantity. Researches showed effective microorganisms promotes the startup of the process.Biofilm in the bioaugmentation process matured with 6 days while biofilm in normal process matured with 9 days. Effective microorganisms could accelerate the degradation of COD and shorten the residence time. Aggrandizement system could make COD<200 mg/L with 6 to8 hours while cntrolling system could make COD<200 mg/L with 8 to 10 hours. Long-term operating shows that SBBR in the bioaugmentation system worked better than the normal system in the treatment of COD and NH4+-N. The average COC of effluent in bioaugmentation system was 53 mg/L, normal system was 74 mg/L. In the simulative circulation process,aggrandizement process, which could fulfill 8 times theoretical circulation, works more stably than controlling process which could only fulfill 4 times theoretical circulation. Researches showed that reasonable design could make the wastewater meet the first grade of discharging standard of National Integrated Wastewater Discharge Standard (GB8976-1996), and partially meet the demand of water using of the factory. Adding effective microorganisms could enhance the biotreatment and make the effluents reuse many times.

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2001~20035606323557.7% AN-P1Rhodococcus sp.AN-P1pH62000 mg/L30 0.3AN-P1500 mg/L1000 mg/L2000 mg/L28 h24 h32 hGB8978-1996SBRCOD10% PCR-DGGEAN-P1 AN-P1 Recent years, environment pollution accidents happened frequently, the data showed that there are 5606 accidents between 2001 and 2003, including 3235 water environment accidents, which is 57.7% of all. These accedents not only caused money lost and life lost but also caused serious damage to the ecologicl environment. So exploring highly-effective and secure methods to solve these accidents is an urgent mission. We screened a highly-effective aniline-degrading bacterium and did some researches on its ability to degrade aniline, in order to guide the emergency treatment of aniline containing wastewater that caused by sudden accident pollution with bioaugmentation. A highly-effective aniline-degrading bacterium AN-P1 was isolate and characterized as Rhodococcus sp. It degrades aniline through meta-cleavage pathway. The optimal pH and temperature for cell growth and aniline degradation were 6 and 30 , respectively, and the opitimal concentration of aniline was 2000 mg/L, the optimal inoculation amount was 0.3.It took bacterium AN-P1 only 18 h, 24 h and 32 h, respectively, for the treatment of MSB containing 500 mg/L, 1000 mg/L, 2000 mg/L aniline to meet the first grade of national some of the NH4+-N which caused by aniline degradation. It took bacterium AN-P1 only 10 h, 20 h and 32 h, respectively, for the treatment of wastewater containing 500 mg/L, 1000 mg/L, 2000 mg/L aniline to meet the first grade of national integrated wastewater discharge standard. The bacterium AN-P1 can also remove some of the NH4+-N which caused by aniline degradation. It took bacterium AN-P1 only 10 h, 20 h and 32 h, respectively, for the treatment of wastewater containing 500 mg/L, 1000 mg/L, 2000 mg/L aniline to meet the first grade of national integrated wastewater discharge standard. By combing AN-P1 with regular SBR system, it took only 36 h for the emergency treatment of wastewater containing 2000 mg/L aniline under simulating engineering conditions to meet the discharge standard. While the NH4+-N of effluent can not meet the standard because of the high amount NH4+-N caused by aniline degradation. The regular SBR system was not good at aniline and COD removal. The removal efficiency of which are less than 10%. It cost 67.8 g activated carbon to absorbed 1000 mg aniline. It is inconvenient to transport and use it for the emergency treatment of aniline when the sudden pollution accident happened. Meanwhile, it was complex ad hard to recycle the activated carbon and treat the aniline wastewater get from activated carbon recycling too. Hard to meet the effluent standard was also a problem of activated carbon absorption method. According to the PCR-DGGE profile and removal efficiency of pollutants and COD when the systerm recover from emergency treatment, AN-P1 can efficiently protect the microbial community of regular activated sludge system against the aniline. It proved that combing AN-P1 with regular biological system is a feasible strategy for emergency treatment of aniline sudden pollution accident. The research offered a new way for emergency treatment of aniline sudden pollution accident.

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10ml0.8M,0.6A/cm2,pH2.5,1h,(IR)(SEM)IR887cm-1,,NH4+NH3,UO2(OH)2.xNH3.yH2OUO2(OH)2-x.(ONH4)x.yH2O,SEM,238U234U,41984773keV,

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212Pb, 133Ba224Ra,(NH4)2H2EDTA,PbBaRa60 MeV/u 18OThO2Ra,,Ba,Ra70%

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Saccharomyces cerevisiae YYHIRFL100MeV/uTTC5T4 1. YY8-20h 2. TTCTTCT4 3. T4pHT422%10%30oC,pH 4.5 ,:NH42SO4 1g/LKH2PO4 5g/LMgSO4 3g/L 4. YY36h8.6% (V/V) T49.8%24hT4

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,DCD1--3,5-(DMHMP),DMHMPDCD,:(1)NH4+-N(P<0.01);(2)NO3--N(P<0.01);(3)pH.DMHMPDCD,DCD,DCD2,DCD.721,DMHMP

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,,3,5-(DMP),,N0.6%1~.0%DMP(0.80~.9g/g,),,,1.0%DMPNH4+-N30%,NO3--N20%N0.8%1~.0%DMP,,DCD(),DMP,

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,3,5-(DMP).,DMP,,DMP,.10 d,DMP(0.002 50.010.025 g/kg)NH4+-NCK5.179.3611.04,NO3--N14 d,CK33.30%61.19%73.72%(p<0.01).NO2--N,3 d DMPNO2--N95.77%~96.13%;10 d,DMP,,DMP1N14~56 d.2 a,20042005,DMP(40~100 cm)NO3--NCK28.77%44.70%.,DMP.

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,(DCD)3,5-(DMPZP).,DMPZP,1.0%(N)NH4+-N,NO3--N.DMPZP,DMPZPDCD,DCD2DMPZP,()DMPZPDCD.DMPZP714,,DMPZP1.0%2.0%(N)71429.3%41.7%18.6%34.3%;,DMPZP30%.DMPZPpH,DMPZPDCDpH.

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,N-(NBPT)3,4-(DMPP),NBPTDMPP,NNH4+-N;,NNH4+-NNO3--NN,NBPTDMPP0.1%0.5%

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SBR,,10000mg/L,SBR;COD_(Cr)7001000mg/LNH4+-N80120mg/L[Cl-]8000mg/L,COD_(Cr)NH3-N77.9%81.2%69.5%76.6%,,,

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,32010cm.:3221%42%45%;511NH4+-N(P=0.001;P=0.019),5811NO3--N(P<0.001;P=0.048;P=0.031);5811CO2-C,(P>0.05);58,11;;,,.32;,..