Ardışık kesirli reaktörlerde biyolojik aşırı fosfor giderimi
Başlık çevirisi mevcut değil.
- Tez No: 55869
- Danışmanlar: DOÇ.DR. NAZİK ARTAN
- Tez Türü: Doktora
- Konular: Çevre Mühendisliği, Environmental Engineering
- Anahtar Kelimeler: Belirtilmemiş.
- Yıl: 1996
- Dil: Türkçe
- Üniversite: İstanbul Teknik Üniversitesi
- Enstitü: Fen Bilimleri Enstitüsü
- Ana Bilim Dalı: Belirtilmemiş.
- Bilim Dalı: Belirtilmemiş.
- Sayfa Sayısı: 209
Özet
ÖZET Tüm gelişmiş ülkelerde azot ve fosfor deşarj standartlarının giderek sıkılaşması, bu standartlara ulaşabilmek için kullanılacak arıtma yönteminin güvenilirliğinin yamsıra ekonomik ve uygulanabilir olması gerekliliğini de beraberinde getirmektedir. Biyolojik aşın fosfor giderimi ise son yıllarda önem kazanmaya başlayan ve düşük maliyeti sayesinde kimyasal fosfor giderimine alternatif olabilecek bir arıtma yöntemidir. Fakat mekanizması ve etkili kontrol proseslerinin tam olarak anlaşılamamış olması nedeniyle teknolojiye uyarlanmaları ülkemizde henüz yeterli düzeye ulaşmamıştır. Ardışık kesikli reaktör sistemleri (AKR) ise biyolojik fosfor giderimi için ekonomik bir çözüm olma potansiyelinin yamsıra laboratuvar ölçeğinde kontrol ve ayarlanabilme imkanı sayesinde BAFG mekanizmasının karmaşık yapısının incelenmesi için çok uygun sistemlerdir. Bu iki noktadan hareketle bu çalışmada BAFG mekanizması, işletme koşullarının iyi tanımlandığı ardışık kesikli bir reaktörde, özellikle atıksu özelliğinin sistem üzerindeki etkileri yönünden incelenerek prosesin daha iyi anlaşılabilmesinde önemli noktalar ortaya konulmuştur. Ayrıca AKR sistemlerinin BAFG amacıyla kullanımına yönelik pratik uygulamalar açısından reaktörün farklı işletme koşullarında çalıştırılmasının etkileri değerlendirilmiştir. Deney sonuçlan değerlendirildiğinde anaerobik/aerobik laboratuvar ölçekli AKR' de protein, asetat ve glukoz içeren sentetik atıksu kullanılarak yüksek fosfor giderme verimlerine ulaşılabildiği görülmektedir. Sistemin KOİ kısıtlayıcı şartlarda çalıştınlması ile çamurun fosfor içeriğinin %16 gibi yüksek değerlere ulaşması mümkün olmaktadır. İyi fosfor gideriminin gerçekleştiği ve anaerobik bölgede salınan fosfor miktannın yüksek olduğu durumlarda UAKM/AKM oranı fosfor içeriğine bağlı olarak 0.6 civannda gözlenmiş olup, fosfor giderme özelliğinin bozulduğu durumlarda bu oran 0.8 - 0.9 değerlerine yükselmiştir. Atıksudaki asetat yüzdesinin azalması ve glukoz yüzdesinin artması sonucu anaerobik bölgede salman fosfor miktarının ve fosfor giderme veriminin düştüğü gözlenmiştir. Buradan anaerobik bölgede polifosfat enerjisini kullanarak substrat depolayan Poly P organizmalannın azalarak polifosfat enerjisi kullanmadan da anaerobik bölgede canlı kalabilen bakterilerin ortamda hakim olduğu sonucu çıkmaktadır. Bu sonuç BAFG sistemleri için anaerobik bölgede fermentasyon ürünlerinin varlığının önemini vurgulamaktadır. Substrat olarak sadece asetat kullanılarak yapılan kesikli deneyler de bu sonucu destekler nitelikte olup, salman fosforun kullanılan asetata mol oranı sistemdeki Poly P organizmalannın fraksiyonuna bağlı olarak 0.03-1.75 gibi çok geniş bir aralıkta değişmiştir. Aerobik bölgede fosfor alımının birinci derece kinetiğine uygun olarak gerçekleştiği ve anaerobik sürenin fosfor şahmı için yeterli uzunlukta olması halinde aerobik sürenin uzatılması ile fosfor giderimde artma gözlenmekle birlikte fosfor alım hızının zamanla katlanarak azalması söz konusu olmaktadır. Bu nedenle reaktördeki anaerobik ve aerobik faz sürelerinin optimizasyonu önem taşımaktadır. Konuyla ilgili yapılacak model simülasyonu deneysel sonuçların değerlendirilmesini daha anlamlı hale getirecektir. XV
Özet (Çeviri)
SUMMARY BIOLOGICAL EXCESS PHOSPHORUS REMOVAL IN SEQUENCING BATCH REACTORS Growing importance has been assigned to the impingement of nutrients on the aquatic environment. The discharge to surface waters of carbon nitrogen and phosphorus stimulate a series of changes in these ecosystems known as eutrophication. The elimination of carbon in wastewater discharges to receiving waters does not rule out the possibility of eutrophication. Thus, it is crucial to control the input of nitrogen and phosphorus. Since some blue-green bacteria have the ability to fix atmospheric nitrogen gas to support primary production, the eutrophication control strategies are generally based upon the control of phosphorus in the effluent discharges to water bodies. In many countries, the legal effluent limitations include both the removal of nitrogen and phosphorus. The European Community's Urban Wastewater Treatment Directive (Council of European Communities, 91/271) prescribes more stringent phosphorus standards for treated wastewaters discharged to sensitive areas. It requires a minimum of 80 % phosphorus removal (or 1-2 mg/1 effluent total phosphorus) together with 70-80 % nitrogen removal. High cost connected with chemical phosphate removal (especially due to extra sludge production and reagent consumption) have given an intensive stimulus to the enhanced biological phosphorus removal (EBPR) process in the activated sludge treatment plants. EBPR is extensively studied since 1970's. However the true mechanism and related effective control of the process is yet to be achieved. Therefore kinetics of enhanced biological phosphorus removal (EBPR) is one of the most intriguing issues of environmental technology today. All the configurations for biological phosphorus removal incorporate alternating anaerobic and aerobic stages. In the anaerobic stage, phosphorus is released from the microorganisms and soluble P concentration increases. The phosphorus release is typically accomplished by an appreciable consumption of organic substrates and does not occur unless oxygen and oxidized nitrogen are both absent. During the aerobic stage, microorganisms uptake the phosphorus and P concentration decreases to a level much lower than the influent. The microorganisms responsible for this process have the ability to store polyphosphates and mostly referred to as Poly-P microorganisms. Many researchers concluded that the phosphorus-storing microorganisms (Poly-P) belonged to the genus of Acinetobacter. Although Acinetobacter has been found to be dominant in excess phosphorus removing plants, many workers have observed that some other genera were also capable of storing polyphosphate such as Aeromonas and Pseudomonas. xviIt is well known that BEPR requires an anaerobic/aerobic sequence and short chain fatty acids (SCFA), for an effective phosphorus removal. Many researchers supported the view that the function of the anaerobic period is to produce fermentation products which are utilizable by the Poly-P bacteria (Deinema et al., 1985 ; Brodish, K. E. U., 1985). Some workers proposed as the primary function of the anaerobic zone, the stressing of the organisms to stimulate the phosphorus release which provides them with the energy needed for substrate uptake and storage and the subsequent phosphorus uptake in the following aerobic zone (Nichols et al., 1979). In this way, the poly-P bacteria can compete for substrate with other bacteria in the system. Since the recognition of excess phosphorus removal in activated sludge system, various biochemical models have been proposed for explaining the process. In all the kinetic models so far proposed, acetate is referred as the sole external substrate which is taken up and stored as poly - P hydroxy butyrate (PHB) during the anaerobic conditions. The synthesis of the PHB from acetyl - CoA requires NADH 2. The question of how a reducing power is created for the PHB synthesis constitutes the main distinction between various biochemical models. According to the Comeau / Wentzel model, the NADH2 can be provided via feeding some of the acetyl - CoA into the TCA cycle (Comeau et al.,1986; Wentzel et al., 1986). The production of one more of acetyl - CoA from acetate entering the cell by passive diffusion requires one mole of ATP energy. Thus, the theoretical P release/acetate uptake ratio is 1 mole P/mole acetate or 3 1 g /64 g COD. Comeau et al. (1987) define this ratio as 1.5 mole P/mole acetate, based upon the assumption 0.5 mole ATP is utilized for substrate transport per mole of acetate. Mino et al. (1987) proposed that the reducing power required for the PHB synthesis is produced through the degradation of the intracellular glycogen stored via the EMP pathway. In the Mino model, 6 moles of acetate uptake theoretically corresponds to the utilization of one mole of intracellular carbon and to the synthesis of 4 moles of PHB monomer. In this model it is also postulated that 3 of the 6 moles of ATP needed to activate 6 moles of acetate, are obtained through EMP pathways. Thus, the amount of ATP to be derived from poly - P is reduced to 3 moles, hence the quantity of P released becomes 3 moles. This corresponds to a P rei / Acetateuptake ratio of 0.5. The released P/acetate uptake values observed in different experimental studies show a variation of 0.05 - 1.5 mole P/ mole acetate. It has been shown that when SCFA other than acetate are used as substrate, other poly - hydroxyalkonoates (PHA) are synthesized besides PHB (Satoh et al., 1992). Randall et al (1994) reported that carboxylic (except propionate) acids were probably the most important fermentation products for inducing and maintaining EBPR. It is generally accepted that poly P microorganisms are unable to directly utilize glucose under anaerobic conditions, in EBPR systems, readily biodegradable substrate consisting of glucose-like materials has to be converted first by the non-poly P microorganisms to SCFAs under anaerobic conditions. However, Randall et al.(1994) reported that the anaerobic phase of the SBRs did not act as a fermentation zone for glucose. This was probably because glucose was rapidly transported into the cells before it could ferment. The reported phosphorus removal results are inconsistent, especially in the case when glucose containing synthetic wastewater is used. Cech and Hartman (1993), observed a group of microorganisms (named G bacteria), which do not contribute to EBPR in lab-scale anaerobic/ aerobic activated xvusludge system fed with a mixture of glucose and acetate. Since G bacteria can take up organic substrates without using polyphosphate, the Prei /COD * ratio decreases due to the ratio of numbers of G bacteria and poly P bacteria. Their accumulation in the activated sludge brings about phosphorus removal deterioration. Matsuo et al.(1992) defined a mechanism for a microorganism using glycogen instead of poly P as the energy source under anaerobic conditions. According to this approach, extracellular glucose, or glucose 1-P, produced from intracellular glycogen is first used to generate two moles of pyruvic acid via the EMP or the ED pathway. One mole of pyruvic acid undergoes decarboxylation through an oxidation reaction, while the other is reduced to propioyl-CoA. Ultimately PHA is synthesized without producing net reducing power. Since this mechanism involves no energy deficit, and even a net production of one mole of ATP, the poly P energy is not essential and the bacteria having this mechanism are able to compete with poly P bacteria for substrates in anaerobic/ aerobic systems. More recently, Satoh et al. (1994), described this metabolism of microorganisms in the failed biological phosphorus removal sludge, and possible strategies to avoid the deterioration of biological phosphorus removal. The above-reported background suggest that better knowledge has to be gained about the EBPR. In this context, it would be misleading to directly relate the EBPR mechanism to the overall readily biodegradable substrate without exploring its nature and composition. This study describes a lab-scale experimentation carried out to study EBPR under well defined conditions and to investigate the effect of different organic substrate combinations, consisting of Tryptone Soya Broth (TSB) having similar characteristics with readily biodegradable fraction of domestic sewage, together with acetate and glucose on the EBPR mechanism in a sequencing batch reactor (SBR). Currently, SBR is promoted as a very promising alternative process with distinct advantages over the conventional activated sludge process. Basically, it is a very simple process and everything is solved in a single tank. Sequencing batch reactor (SBR) technology offers an additional advantage for EBPR process, since it is temporally controlled as contrasted to spatially controlled conventional continuous biological treatment processes and temporal control provides a clear understanding and interpretation of the variation of significant process parameters with time. Therefore, SBR appears to be well suited process for the acquisition of a better understanding of enhanced biological phosphorus removal, for process simplicity, flexibility and control. This way, it is also possible to propose a design strategy and a procedural approach for a given wastewater, for practical implementation. Experimental Study The experimental work was carried out in a lab-scale sequencing batch reactor (SBR) having anoxic anaerobic, aerobic conditions. The mixed liquor volume at the end of fill period was 8.8 1 and after draw 3.4 1. The synthetic wastewater fed to the system consisted of different combinations of TSB, sodium acetate and glucose. Additional nutrients and minerals, including inorganic phosphorus and nitrogen were also added xvuito the feed solution. The feed was prepared daily by using tap water. Experimental work can be evaluated by dividing into 4 main step: 1. Start up period (Growth of Poly-P organisms) 2.Determination of maximum phosphorus storage capacity (COD limiting conditions) 3. The influence of different substrates on EBPR under COD limiting conditions. 4.The effect of different operational conditions of SBR on EBPR 1. Start up period During the start up period, SBR was operated with a cycle time of six hours. Each cycle included 15 minutes static fill, lh 30 minutes anaerobic mixing (initially anoxic) 2 h 30 minutes aerobic react phase, 1 hour settling and 45 minutes draw and idle phase. For starting up the system, reactor was seeded with activated sludge taken from a fully aerobic activated sludge plant. Biomass concentration was kept about 2000 mgVSS/1 at 5 days sludge age. The synthetic wastewater fed to the system consisted of only TSB (450 mg/1 COD) at the beginning. After four weeks of operation EBPR was established in the system using 450 mg/1 TSB and 50 mg/1 acetic acid. TSB concentration was decreased to 240 mg/1 and 260 mg/1 sodium acetate was added at later stage to improve the growth of Poly-P microorganisms. However, when the influent acetate was increased to 260 mg/1, the phosphorus removal decreased and sludge settleability worsened. Influent total phosphorus was 26 mg/1 at the beginning and 6 mg/1 at the end of start up period. After 120 days, Poly-P organisms became dominant and phosphorus released in the anaerobic phase increased to 22 mg/1 and all of the soluble phosphorus was removed in the aerobic phase. The influent acetate concentration than was reduced to 60 mg/1 COD equivalent from 260 mg/1 COD equivalent at the end of start up period. The phosphorus content of the sludge was 3.2 % on S S basis and 3.7 % on VS S basis. This condition was considered as the beginning of the experimental study and each different wastewater composition with a certain operational condition was referred as a SET. 2.Determination of maximum phosphorus storage capacity The sludge age was controlled at about 8 days by wasting 1-1.1 1 of mixed liquor everyday. Biomass concentration was maintained at between 1.9 - 2. 1 g/l VSS during this period. The system was operated over 150 days until it reached maximum phosphorus storage capacity and become COD limiting by increasing the influent phosphorus concentration gradually while keeping the influent COD concentration constant at about 300 mg/1 (240 mg/1 TSB and 60 mg/1 sodium acetate). As the influent phosphorus concentration increased, released phosphorus in the anaerobic phase (Prei) and the phosphorus content of the sludge increased until COD became limiting. The VSS/SS ratio also decreased as the phosphorus content of the sludge increased. The results of these sets are given in Table 1. The operational mode of the reactor was the same as given for start up period. XIXTable 1 The Average Results (SET 1 - SET 6) SETİ SET 2 SET 3 SET 4 SET 5 SET 6 3.The influence of different substrates on EBPR under COD limiting conditions. As can be seen from Table 1, the system reached its maximum P storage capacity at about 16 mg/1 influent P concentration. Then the influent P concentration was increased to 20 mg/1 and kept constant during the study resulting in a residual effluent P concentration of around 4 mg/1 and allowing this way to evaluate the effect of different substrates on the efficiency of P removal. The P content of the sludge was 9.6 % on SS basis and 14.8 % on VSS basis with a corresponding VSS / SS ratio of about 0.65 at the beginning of this step (SET 6). Then the different substrate combinations of TSB, acetate and glucose were tried (SET 6 - SET 12). The wastewater compositions during 3. step of the study are given in Table 2. Table 2 Synthetic Wastewater Compositions *Other micronutrient concentrations were the same during all sets and amounts added were as follows: Mg: 3 ; Ca: 1.4 ; Fe:0.2 ; Mn: 0.26 ; Zn:0.22 mg/1 (excluding the amounts coming from tap water). System performance was observed in two different ways, namely, continuous monitoring of the SBR system performances and batch tests conducted with the sludge wasted from the aerobic phase of a SBR cycle. The parameters measured for the monitoring were COD, TKN, Total Phosphorus, P04-P, NH4 -N and NOx-N. All analysis were carried out according to Standard Methods (APHA, 1989 ). xxContinuous SBR Tests Figure 1 shows daily variations in phosphorus parameter from SET 6 to SET 12. Average results of the experimental study for each SET are also given in Table 3. When the acetate addition in SET 6, with the feed solution containing 80% TSB and 20% acetate, was ceased and compensated with TSB (SET 12) the system performance was deteriorated because of both the increase in the influent TKN concentration and also the lack of the acetate. And then, the same acetate concentration was added for the recovery of the previous system performance. When the system restabilized, the acetate concentration was reduced by half and glucose was added instead (SET 7). It was observed that the addition of glucose instead of acetate did not yield the same phosphorus removal despite the fact that the COD/P ratio did not change and consequently effluent P concentration was observed to increase from 4 mg/1 to 8.5 mg/1. When glucose addition was stopped (SET 8) although COD/P ratio decreased, the system performance was similar to that glucose concentration increased to 20 % of total COD and COD/P ratio was again maintained at 15 (SET 9+10). Phosphorus concentration at the end of anaerobic phase decreased as the glucose fraction in the feed solution increased from 20 % to 50 % in SET 11. As a result, effluent P concentration increased to 13 mg/1. There was no significant variation in COD utilization between the sets. Almost all of the COD disappeared after the anaerobic phase, with a small residual portion at the end of the cycle. However Prei / COD* ratio decreased by increasing the glucose fraction in the feed as can be seen from Table 3. As parallel to P removal efficiency, P content of the sludge also decreased from 15 % in SET 6 to 6.8 % in SET 11 on VSS basis. Typical COD, NOx-N, NH4-N and P profiles throughout a complete cycle for two selected sets ( SET 6 and SET 1 1) are illustrated in Figs. 2 and 3. 60 50 ? ~ 40 o> E r 3o 1 o Q- 20 10 - SET 6|SET| 12 SET 6 SET SETS SET 9+10 JlJ-k^ SET 11 - Feed(TP) -Anaerobic -Aerobic 150 160 170 180 190 200 210 220 230 240 250 320 330 340 Time (days) Figure 1. Daily variations in phosphorus parameter XXITable 3 Average Results (SET 6-SET 12) aerate 90 120 150 180 210 time (minutes) Figure 2. Typical COD, P04-P, NOx-N and NH3-N time profiles during SET 6 xxii300 250 200 O 150 8 I ıoo 3 50 30 60 90 120 150 180 210 240 270 time (minutes) Figure 3. Typical COD, P04-P, NOx-N and NH3-N time profiles during SET 1 1 Batch Tests Anaerobic batch tests were conducted as additional support to previous observations on SBRs to visualize the effect of different types of substrate on phosphorus release. The batch experiments were coupled to a number of continuous sets as shown in Figs. 4 and 5 each having a different poly-P microorganism ratio. 250 250 £T 200 & ~ 150 £ 100 d R 50 60 120 180 time (minutes) 240 60 120 180 time (minutes) 240 (a) (b) Figure 4. COD, P04-P time profiles of the batch tests fed with acetate (a) and glucose (b) during SET 7 xxniO 30 60 90 120 150 180 210 240 time (minutes) 30 60 90 time (minutes) 120 (a) (b) Figure 5. COD, P04-P time profiles of the batch tests fed with acetate (a) and glucose (b) during SET 1 1 This way it was possible to see the effect of bacterial population dynamics on the magnitude of P release. It is interesting to compare the results illustrated on Figs 4 and 5 both fed with acetate and glucose. In the experiments coupled with SET 7 (Figure 4) sustaining a relatively large portion of poly-P microorganisms, Prei/CODut ratio was 0.7 mg/mg when fed with acetate whereas in the experiments coupled with SET 1 1 (Figure 5) practically devoid of these type of organism, the same acetate feeding only produced a ratio of Prei/CODut 0.014 mg/mg. Phosphorus release with glucose feeding were as expected much lower in all the experiments. 4. The effect of different operational conditions of SBR on EBPR Until this part of the study, reactor was operated with 6 hours cycles and 4 cycle in one day. In order to see to what extend the system performance is affected by the operational conditions, the number of the cycles was decreased to 3 in a day to have longer cycle times (8 hours) allowing different anaerobic/aerobic phase applications. Different operation applications and their results are given in Table 4. Although longer aerobic phase times resulted in better phosphorus removal efficiency, the average phosphorus uptake rates decreased. It is important to select the optimum anaerobic phase time just enough to allow the release of phosphorus. If it is too long, since P release stays constants, Pupt/Prei ratio does not increase and the system is considered as overdesigned. When SET 10 and SET 13 are evaluated, it can be concluded that SET 13 is overdesigned comparing to SET 10. XHVTable 4 Average Results of Different Operational Conditions Evaluation The experimental results show that high EBPR can be obtained in a lab-scale anoxic / anaerobic- aerobic SBR using synthetic wastewater containing acetate, protein and glucose. System can be operated under COD limiting condition to use the maximum storage capacity of the sludge depending to COD/P ratio. The COD/P ratio found to be 20 allowing to achieve phosphorus storage limiting condition. The phosphorus content of the sludge was as high as 16 % on VSS basis under COD limiting conditions which also results in low effluent phosphorus concentration as long as the maximum storage capacity of the sludge is not exceeded. The ratio of the VSS/SS can be used to monitor phosphorus removal efficiency of the system as an indicator showing the changes in the P content of the sludge since a good correlation was observed between effluent P concentration and VSS/SS ratio. While the ratio in the system having a good phosphorus removal is about 0.60, it is increased to 0.8- 0.9 as the Poly P organisms ratio and P content of the sludge decreases. The Pupt/Prei ratio is also very important indicating which system is dominant. If the phosphorus release occurs and the Poly P bacteria are dominant in the system Pupt/Prei ratio is constant at about 1.30. The increase in this ratio can be attributed to two reason. One reason is the increase in the aerobic/anaerobic phase ratio which indicate the improvement of the removal efficiency as well. The second reason is the decrease in the phosphorus released in the anaerobic phase resulting with the deterioration of excess phosphorus removal and showing the normal metabolic phosphorus uptake. The maximum phosphorus that can be released was found to be the 50-60 % of the phosphorus content of the sludge under the condition which the substrate concentration consisted of 100 % of acetate. XXVPhosphorus removal capacity of the system gradually declines as acetate addition is lowered and compensated with glucose. It seems that system tolerates the glucose to some extend which is about 20 % of influent COD fraction. If this fraction exceeds 50 % system performance is significantly deteriorated. Further decrease on the removal of phosphorus when the glucose addition is stopped may be explained by the inadequacy of the influent total COD implying that glucose can be converted to SCFA in the anaerobic phase of the SBR. When the influent TKN/COD ratio increases with the resulting increase of NOx-N input to the anaerobic phase, the phosphorus removal efficiency is also observed to decrease due to reduced fermentation. It is also noted that the system performance deteriorates with a glucose rich influent regardless of the fact that the NOx-N input decreases. This is probably due to shifts of the microorganisms type distribution. If the influent wastewater contains less amino acids and proteins the growth of the poly-P microorganisms may become slower in accordance with similar previous explanations (Satoh et al. 1994) and there may be more chance for the microorganisms using glycogen instead of polyphosphates as the energy source to become dominant. The most importance evidence of this conclusion is the results of the batch tests conducted parallel to SBR operation. The range of Prei/CODm ratio is found 0.03 - 1.73 mole/mole in these batch tests. This range covers all the reported results so far. It is important to note that all the experiments were conducted in mixed cultures obtained from activated sludge and enriched in Poly P bacteria through anaerobic- aerobic sequence. Since“/'/ is impossible to say which microorganism does what”(Jenkins and Tandoi, 1991) all these results should be evaluated considering their conditions in detail and design strategies for a given wastewater should be determined very carefully with support of experimental treatability examinations. The SBR systems seem very convenient for enhanced biological phosphorus removal since the operational mode can easily be changed to meet the effluent standard. The batch tests conducted with domestic wastewaters also show that good phosphorus removal can be achieved in SBR system in which Poly P bacteria are enhanced by using a synthetic wastewater having similar characteristic with domestic wastewater. It is suggested to apply these systems for biological phosphorus removal for achieving more reliable results with less investment cost considering the economical conditions of our country. XXVI
Benzer Tezler
- Ardışık kesikli reaktörlerde biyolojik aşırı fosfor giderimi üzerine oksitlenmiş atotun etkisi
Başlık çevirisi yok
NEVİN ÖZGÜR
- Ardışık kesikli reaktörlerde uygulanan faz sürelerinin evsel atıksularda biyolojik aşırı fosfor giderimine etkileri
The Effects of operation phase periods in sequencing batch reactors on biological excess phosphorus removal from domestic wastewater
CEM ÇAKIR
Yüksek Lisans
Türkçe
2002
Çevre MühendisliğiGebze Yüksek Teknoloji EnstitüsüÇevre Mühendisliği Ana Bilim Dalı
PROF. DR. MEHMET KARPUZCU
- Karbon kaynağının ve katyon dengesinin biyolojik aşırı fosfor giderimi prosesi ve aktif çamurun çökme performansına etkisinin değerlendirilmesi
Evaluation of the effect of carbon source and cation balance on the enhanced biological phosphate removal and the settling performance of activated sludge
HÜSEYİN YAZICI
Doktora
Türkçe
2014
Çevre MühendisliğiSüleyman Demirel ÜniversitesiÇevre Mühendisliği Ana Bilim Dalı
DOÇ. DR. MEHMET KILIÇ
- Hydraulic-and/or metabolic-selection pressures influenced aerobic granulation and its application in enhanced biological phosphorus removal (EBPR)
Hidrolik-ve/veya metabolik-seçme baskıları etkisiyle aerobik granülasyon oluşumu ve biyolojik aşırı fosfor giderimindeki (BAFG) uygulamaları
EBRU DÜLEKGÜRGEN
Doktora
İngilizce
2006
Biyoteknolojiİstanbul Teknik ÜniversitesiÇevre Mühendisliği Ana Bilim Dalı
PROF.DR. NAZİK ARTAN