On-line Monitoring for Phosphorus Removal Process and Bacterial Community in Sequencing Batch Reactor

BIOTECHNOLOGY AND BIOENGINEERING Chinese Journal of Chemical Engineering, 17(3) 484ü492 (2009)

On-line Monitoring for Phosphorus Removal Process and Bacterial Community in Sequencing Batch Reactor* CUI Youwei (Ӂပน)1, WANG Shuying (ฆೞ࿭)1,** and LI Jing (ह࠶)2 1 2

Key Laboratory of Beijing for Water Quality Science and Water Environment Recovery Engineering, Beijing University of Technology, Beijing 100124, China China Aeronautical Project and Design Institute, Beijing 100011, China

Abstract For efficient energy consumption and control of effluent quality, the cycle duration for a sequencing batch reactor (SBR) needs to be adjusted by real-time control according to the characteristics and loading of wastewater. In this study, an on-line information system for phosphorus removal processes was established. Based on the analysis for four systems with different ecological community structures and two operation modes, anaerobic-aerobic process and anaerobic-anaerobic process, the characteristic patterns of oxidation-reduction potential (ORP) and pH were related to phosphorous dynamics in the anaerobic, anoxic and aerobic phases, for determination of the end of phosphorous removal. In the operation mode of anaerobic-aerobic process, the pH profile in the anaerobic phase was used to estimate the relative amount of phosphorous accumulating organisms (PAOs) and glycogen accumulating organisms (GAOs), which is beneficial to early detection of ecology community shifts. The on-line sensor values of pH and ORP may be used as the parameters to adjust the duration for phosphorous removal and community shifts to cope with influent variations and maintain appropriate operation conditions. Keywords on-line monitoring, phosphorus removal, sequencing batch reactor, pH, oxidation-reduction potential

1

INTRODUCTION

Phosphorus pollutants in wastewater are responsible for increasing the eutrophication in surface waters, which results in a great financial loss and potentially ill effects on health. The enhanced biological phosphorus removal (EBPR) process is considered as a cost effective and environmentally friendly technology to remove phosphorous from wastewater. EBPR is based on the enrichment of phosphorus accumulating organisms (PAOs) [1]. It has been demonstrated that the biological population in phosphorous removal comprises of at least two groups: one group utilizing either oxygen or nitrate as an electron acceptor (denitrifying PAOs), and the other utilizing only oxygen (aerobic PAOs) [25]. In the anaerobic phase, PAOs take up volatile fatty acids (VFAs) and store them as polyhydroxyalkanoates (PHAs). The energy for this anaerobic process is from the hydrolysis of intracellular polyphosphate and the glycolysis of glycogen followed by the release of ortho-phosphate to the bulk liquid [6]. In the subsequent aerobic/anoxic phase, PAOs use oxygen or nitrate as an electron acceptor and use PHAs to generate energy for growth, glycogen synthesis, and phosphate luxury uptake [7, 8]. Therefore, EBPR can be achieved by altering anaerobicaerobic (A/O) or anaerobic-anoxic (A/A) conditions. As one of EBPR processes, a sequencing batch reactor (SBR) has some advantages, e.g., single-tank design and the flexibility for different treatment objectives, by adjusting the duration of anaerobic, anoxic and

aerobic phase to achieve the EBPR effect. The SBR is well suitable for relatively small amounts of wastewater to be treated, while it also performs satisfactorily in larger applications [9, 10]. However, the flexibility in operation requires a higher level of process control and automation management. An important aspect in SBR process management is the duration control of batch mode or step timing. Biological wastewater treatment plants (WWTPs) are normally designed and operated under nominal operating conditions, in which the loading rate is assumed constant [11, 12]. The SBR is also operated on a fixed-time schedule, but this steady-state assumption is inappropriate since the process is subjected to fluctuations in flow rate and loading. The primary drawback is the inapplicability for adjusting the cycle duration in the process according to the characteristics and loading of wastewater, which will result in an inefficient operation, i.e., inefficient energy consumption or poor control on the effluent quality. Moreover, inadequate timing may result in serious process degradation, especially in phosphorous removal [13]. A possible control strategy is based on the real-time measurement of relevant process variables, i.e., COD, ammonium-N, nitrate-N and phosphate-P, to identify the end of a biological reaction. However, there is a formidable obstacle in this scheme, represented by the complexity in on-line measurement of the variables, which is neither simple nor economical [10]. For this reason, in recent years, it has been received much attention to use oxidation-reduction potential (ORP), pH and dissolved oxygen (DO) as the parameters for real-time control of

Received 2008-09-04, accepted 2009-04-09. * Supported by the Project of Scientific Research Base and Scientific Innovation Platform of Beijing Municipal Education Commission (PXM2008_014204_050843), the National Natural Science Foundation of China (50808004), and the Doctoral Startup Research Program of Beijing University of Technology. ** To whom correspondence should be addressed. E-mail: [email protected]

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the cycles in SBR systems [1432]. It has been shown that the ORP and pH pattern under a given wastewater treatment conditions can be used as indirect process indicators to identify specific control points, in particular, in biological nitrogen removal process [1427]. However, very little work has been conducted on the real-time control of SBR systems for phosphorous removal, although their inherent time-oriented nature and the available automatic control equipment make the attempts quite attractive. The reasons may be related to (1) many factors affecting the phosphorous removal process [33, 34], and (2) the microbial competition between PAOs and GAOs in EBPR ecology community. In recent years, poor performance or even complete failure of EBPR processes has been reported. In addition to conventional factors affecting the process, GAOs as a potential competitor to PAOs in EBPR system has attracted considerable interest [3540]. GAOs can compete effectively with PAOs under anaerobic-aerobic conditions. However, GAOs do not store polyP and use glycogen as their sole energy source for VFA uptake. Consequently, the identification of specific control points becomes complicated because phosphorous removal is highly dependent on the competition behavior in EBPR ecology community. Therefore, on-line monitoring and detection of the state of ecology community is required for successful control of EBPR SBR to make the process more effective. A few studies on control of EBPR SBR reported that the profile of OPR and pH could give signals for controlling phase duration in activated sludge in treating synthetic wastewater under A/O condition [10, 2832]. However, these studies were limited to the treatment of synthetic wastewater, investigation on the sole community highly enriched by PAOs, and application of A/O cycle to develop the control strategy for phosphorous removal, which is insufficient for practical applications. A complete control system should be developed based on the application of real wastewater, the investigations on various microbial communities and all phosphorous removal processes (A/O and A/A cycle mode). Besides, on-line monitoring of population shift should be added to control the phosphorous removal process. These considerations will make the control system more effective, reliable and safe. Based on the above concepts and analysis, the objectives of this study are to establish an on-line information system for phosphorous dynamic control using ORP and pH as parameters under A/O and A/A conditions, and to detect the state of EBPR community by the on-line parameters. For this purpose, four bench-scale SBR systems fed with actual sewage are used and evaluated in three cases of EBPR community Table 1

and two operation modes. 2 2.1

MATERIALS AND METHODS Reactor and operation

Four lab-scale SBRs with working volume of 10 L were inoculated with sludge from a lab-scale modified University of Cape Town (MUCT) process, which purified the domestic wastewater well (the mean removal efficiency for phosphorous and nitrogen is 93% and 74%, respectively). Three reactors were operated under A/O conditions in parallel and the other under A/A cycle. All SBRs were placed in a room with the temperature controlled at 18 to 22qC. These reactors were equipped with ORP, pH and DO electrodes, which were positioned 6 cm below the liquid surface in the reactor. A data acquisition program was used to continuously store and record the measured data on a personal computer. These reactors were operated with the mixed liquor suspended solids (MLSS) at ˉ 25003000 mg·L 1. The effective sludge age (SRT ) was controlled on about 10 days. The cycle of each SBR involved in 6 min feeding, 0.5 h decanting and 2.4 h settling, while the reaction time was flexible according to experimental design and objectives. In each cycle, the volumetric exchange ratio in the reactor was 100%. During the anaerobic phase, the content of the reactor was kept in suspension using a low speed mixer fixed in the reactor. During the aerobic phase, aeration was introduced into the reactor though fine bubble diffusers fixed at the bottom of the reactor and connected to a pneumatic compressor. The air flow rate at the inlet was controlled by a mass flowmeter. In the anoxic phase, to obtain the electron acceptor, sodium nitrate was added into the SBR at the beginning of anoxic phase. The different process sequence in the operating cycle was controlled manually. All reactor systems were operated daily. After a start-up period of 30 days, the SBR was continuously operated for more than 90 days. 2.2

Composition of domestic wastewater

The feed wastewater was collected from the residential area of Beijing University of Technology, Beijing, and first treated in the septic tank. The organic content in the wastewater was moderate, but the total nitrogen content was high. During the investigation period for more than three months, 60 influent samples were analyzed. The composition of domestic wastewater used is presented in Table 1.

Characterization of domestic wastewater

pH

COD

BOD5

TN

NH 4 -N

NO 2 -N

NO3 -N

range

7.27.7

190325

102180

5195

3285

0.050.30

0.050.84

mean value

7.4

258

165

74

52

0.13

0.43

Note: All values are in mg·Lˉ1 except pH; No. of samples is 60.

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Analytical methods

The reactors were monitored by chemical analytical techniques. Samples withdrawn from the liquid medium during processing were centrifuged at 3000 ˉ r·min 1 for 5 min to remove the bio-solid. Most routine chemical analyses (i.e. PO34 -P , TN, NH 4 -N , NO3-N , NO 2 -N , COD) were conducted according to the standard methods. ORP, DO and pH were measured with WTW inoLab Oxi level2 hand-held instruments. 2.4

Cultivation of bacterial community

Domestic wastewater usually contains a carbohydrate and an organic acid mixture, which are used as carbon and energy sources in biological treatment. Previous studies have the consensus that GAOs often compete with PAOs for carbon sources in A/O systems [41, 42], supported by various accepted biochemical models [43, 44]. Operated properly, the EBPR process can reach relatively high phosphorous removal efficiency. However, under certain circumstances the EBPR system may experience upsets and deterioration. The breakdown of EBPR was found to be due to the outgrowth of GAOs overwhelming PAOs in lab-scale reactors [38, 4548] and in wastewater treatment plants [47, 4951]. Mino et al. [52] proposed a metabolic model for the breakdown of EBPR by GAOs, and the process deterioration was attributable to the presence of GAOs [36, 38, 4752]. How to establish PAOs and GAOs enriched communities was addressed [3542]. It was found that carbon sources favored PAOs over GAOs based on the difference in their abilities to utilize different carbon source. Some carbon sources, such as acetate, offered a competitive advantage to PAOs with respect to GAOs [35, 36, 42], while glucose could not be used as the sole carbon for phosphorous release [3739]. In additions, Liu et al. [37] indicated that the P/C feeding ratio strongly affected the dominance of PAOs and GAOs in the community. Higher ratio seemed to favor the growth of PAOs, while lower ratio resulted in a shift of the dominant population to GAOs. All above studies showed that the predominance of PAOs was attributable to good performance, while the predominance of GAOs was related to deteriorated performance by 16S rRNA/DNA-based molecular methods. Therefore, adjusting the competitive ability of PAOs and GAOs Table 2 Cultivation period feed

by selecting carbon sources fed to the EBPR system is a promising means. In this study, these methods to control the proliferation of GAOs or PAOs were adopted. During the cultivation period, three A/O SBRs, SBR1, SBR2 and SBR3, were fed with different wastewater by adding glucose or acetate into domestic wastewater, which also resulted in the change of the P/C ratio in influent to form different selections to EBPR community (Table 2), as the previous studies [36, 37]. After a 30-days cultivation period, the same domestic wastewater was fed into the three SBRs in the experimental period. The performance in SBR2 kept deteriorating to about 50%. Over 90% phosphorous removal was obtained in SBR3 and 85% for SBR2. According to the reports [3542], this was due to the dynamic shift of EBPR population structure. From the conditions established for controlling growth of GAOs or PAOs [36, 37], it can be concluded that PAOs were dominant in SBR3, GAOs were dominant species in SBR2, and PAOs and GAOs coexisted in SBR1. In SBR4, A/A cycle was applied to cultivate denitrifying PAOs (DPAOs) with the actual domestic wastewater (Table 2). At initiation of the anoxic phase, some sodium nitrate was added into SBR4 so that the electron acceptor (nitrate) was available for DPAOs. 3 3.1

RESULTS AND DISCUSSION SBR systems in A/O mode

PAOs store phosphorus under sequential anaerobicaerobic conditions. VFA are taken up anaerobically and stored as PHA through the release of phosphorus (P) and degradation of glycogen. More P is taken up when an electron acceptor is supplied in aerobic phase. Biochemistry of PAO strongly influences the pH and ORP value in SBR, so that it is important to find the relation between on-line parameters and the extent of biological metabolism for realizing on-line control. 3.1.1 Characteristic pattern of ORP profile The ORP was monitored online to determine its variation in the bio-process of phosphorus release and uptake during anaerobic and aerobic phases. Fig. 1 presents the ORP variations during a typical cycle for different microbial groups. The pattern of ORP does not vary significantly regardless of different phosphorous removal capability in A/O cycle. Under anaerobic conditions, ORP decreases to negative values, below

Controlled conditions Experimental period

P/C ratio

Feed

P/C ratio

domestic

0.080.18

SBR1

domestic

0.080.15

SBR2

domestic and glucose

0.0270.062

domestic

0.080.15

SBR3

domestic and acetate

0.0270.058

domestic

0.10.18

SBR4

domestic

0.090.17

domestic

0.090.17

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(a) SBR1

(b) SBR2

in the aerobic phase, ORP increases with DO. Since the bioprocess involves carbon oxidation, ammonium oxidation and phosphorous uptake, it is difficult to distinguish the biodegradation process of PAOs from other aerobic microorganism. However, in the anaerobic phase, the bioprocess involves acetate uptake and phosphorous release in an EBPR system. It is easier to relate OPR value to phosphorous concentration. In the anaerobic phase, the ORP profile exhibits two stages: the initial sharp decrease in one hour and a slow decrease until the end of anaerobic phase, which is different from that observed by Lee et al [28]. In their experiments, the ORP decreased sharply within an hour and then reached a plateau value, in which the inflection point of ORP profile in the anaerobic stage coincided with the end of phosphate release. In this study, OPR decreases continuously even after the phosphorous release has finished. There is no obvious breakpoint in the ORP profile, and relationship between the decrease of ORP and the increase of phosphate concentration is linear (Table 3). From the linear relation, the concentration and release rate of phosphorous can be estimated and predicted. Since a larger decrease rate of ORP corresponds to more phosphate release, the inflection point corresponding to the end of phosphorus release can be determined by the first derivative of the ORP curves (Fig. 2). In all experiˉ ments, d(ORP)/dtı 0.2 min 1 is statistically the infection point to identify the end of phosphorus release. Therefore, ORP profile can provide some valuable information about the behavior of PAOs to determine the anaerobic duration. Table 3

Linear regression equation in anaerobic phase

Reactor Linear regression equation

R2

x

y

SBR1

y

0.0564 x  0.3427

0.9623 '(ORP) ' (PO34 -P )

SBR2

y

0.087 x  0.3273

0.9801 '(ORP) ' (PO34 -P )

SBR3

y

0.1399 x  1.5067

0.9187 '(ORP) ' (PO34 -P )

SBR4

y

0.0699 x  14.418

0.9603 '(ORP) ' (PO34 -P )

Note: '(ORP), decrease of ORP; ' (PO34 -P ) , increase of orthophosphate.

(c) SBR3 Figure 1 Relation of ORP with phosphorous concentration in different SBRs

100 mV. With aeration, ORP increases to positive values and increases continuously in whole aerobic phase. This indicates that the parameter is closely related to the biological community that is dominant in each system. The parameter ORP, a measure of the oxidative state in an aqueous system, reflects the concentration of DO, organic substrate, activity of organism and some toxic compounds in the system, among which the DO concentration is more important. It is reported that the ORP value is correlated with the logarithm of DO concentration in a linear relationship [40]. Therefore,

Figure 2 The first derivative of ORP with time curves in the anaerobic phase

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3.1.2 Characteristic pattern of pH profile For different microbial community, pH profiles in the anaerobic stage are different (Fig. 3). This observation is not in agreement with previous studies, in which pH decreased as the phosphorous release increased [2429]. This may be explained by the highly-enriched PAOs sludge used in their studies. In this study, the activated sludge system was cultivated to form three community structures composed of PAOs and GAOs. Some bioprocesses that can affect pH in anaerobic and aerobic phase are exhibited in

Table 4. In anaerobic phase, VFA uptake and CO2 stripping increase pH, while phosphorous release and CO2 production decrease pH. In aerobic phase, phosphorous uptake is important to variations of pH. GAOs show similar features as PAOs, but they produce different PHA and lack the ability of EBPR or poly-P accumulation. Since both PAOs and non-PAOs utilized fatty acid in the anaerobic stage, the amount of acid, population size of PAOs, and population size of non-PAOs determined the pH variation because all the conditions were the same in the three SBRs except the ratio of PAOs and GAOs. Table 4

Effect of bioprocess on pH in EBPR Biological process Effect on pH

anaerobic phase

VFA uptake

pH increased PAOs or GAOs

phosphorous release pH decreased CO2 production CO2 stripping aerobic phase

(b) SBR2

(c) SBR3 Figure 3 Relation of pH with phosphorous concentration in different SBRs

pH decreased PAOs or GAOs pH increased

mixer PAOs

nitrification CO2 stripping anoxic phase

PAOs

phosphorous uptake pH increased CO2 production

(a) SBR1

Induced by

pH decreased

nitrifiers

pH decreased carbon oxidation pH increased

aeration

phosphorous uptake pH increased

DPAOs

denitrification

pH increased

denitrifiers

CO2 production

pH decreased

DPAOs

CO2 stripping

pH increased

mixer

In the anaerobic phase, there are four EBPR events affecting pH (Table 4). CO2 is produced by glycogen degradation and decreases pH, while CO2 stripping increases pH. With about the same MLSS in three SBRs, almost the same amount of CO2 is produced in the three systems. The amount of CO2 stripping is also equal under the same aeration conditions. Therefore, the amount of CO2 in the system (CO2 production-CO2 stripping) is almost the same. It indicates that different patterns of pH profile in the anaerobic phase are resulted from the relative amount of VFA uptake and phosphorous release. Although PHA is taken up by PAOs with the correspondent proton, pH decreases due to the phosphorus release. GAOs also take up PHA with the correspondent proton, but as polyphosphate is not involved in GAOs metabolism, phosphorus is not released and pH increases. In SBR1 [Fig. 3 (a)], the pH curve shows a sharp decrease stage and a subsequent even stage. The sharp decrease in twenty minutes is due to the rapidly released phosphorous by PAOs and the plateau is due to the balance between phosphorous released by PAOs and VFA uptake by PAOs and GAOs. In SBR3 [Fig. 3 (c)], the pH curve has a sharp increase in about 5 min and then a sharp decrease. With highly-enriched PAOs, the decrease by phosphorus release is more than the increase by VFA uptake, so that pH decreases as phosphorous

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release increases. The sharp increase is due to the denitrification of residual nitrate or nitrite from the previous cycle, which has been proved in some studies [21, 25, 28, 30]. In SBR2 [Fig. 3 (b)], the pH value decreases in a short time and then increases. With highly-enriched GAOs, although PAOs release phosphate, resulting in proton release to the medium, more protons are utilized during VFA uptake by GAOs and PAOs. The short-time decease in pH profile is induced by metabolism of the small amount of PAOs in the system, which is similar to SBR1. Therefore, a net increase in pH is exhibited in SBR2. Since the pH variation in the anaerobic stage depends on the ratio of PAOs and GAOs population, it can be used for community monitoring by on-line diagnosis, which is important to detect the faults so as to make the adjustment in good time. In the aerobic phase, pH profiles are similar in the three SBRs, with a rapid increase, a subsequent decrease, a rapid decrease and a plateau. The relevant aerobic EBPR processes are phosphorus uptake for poly-P formation, glycogen restoring from PHA resources, PAO growth, lysis and decay. Among them, phosphorus uptake has the highest energy requirement, which is provided by PHA oxidation. According to the biological events occurring in the aerobic phase, the first rapid increase in pH is due to CO2 stripping. The first decrease in pH is resulted from the decrease due to nitrification and the increase due to phosphorous uptake. The valley signals the end of ammonium oxidation (data not shown). The second increase in pH is due to phosphorous uptake. When phosphorous uptake terminates a plateau appears since all aerobic biological events have finished. The knee points (point A, B and C in Fig. 3) in pH profiles indicate the end of phosphorous uptake. 3.2

anaerobic-anoxic cycles to understand the process dynamics. The behavior in the operation is similar to that of the on-line ORP and pH profile shown in Fig. 4. In the anaerobic phase, phosphorous release results in a decrease in ORP, similar to the situation in A/O SBR. The linear relation between the increase of phosphorous release and the decrease of ORP also holds (Table 3). ˉ d(ORP)/dtı 0.2 min 1 corresponds to the infection point to identify the end of phosphorus release (Fig. 2). The continuous decrease of pH is caused by phosphorous release, which indicates that DPAOs are in majority in the ecology community.

3

ƹPO 4

(a) pH -P;ƶNO3 -N; üü pH

SBR systems in A/A mode

The existence of PAOs that utilize nitrate as an electron acceptor instead of oxygen has been confirmed experimentally and practically [7]. The merits of the anoxic phosphate removal are that both N and P are removed in the same process. Compared to conventional EBPR, simultaneous denitrification and P removal can minimize sludge disposal, and reduce aeration and the demand for carbon sources. The enrichment of DPAOs can be achieved by A/A cycle mode. In the anoxic phase, nitrate was introduced into the SBR to provide electron acceptor. In a WWTP, the nitrate required for phosphorous uptake is determined by the amount of ammonium in influent and the phosphorous concentration at the end of anaerobic phase. According to the amount of electron acceptor and the phosphorus concentration at the end of anaerobic phase, two cases were investigated. 3.2.1 Deficient nitrate for phosphorous uptake The process parameters (ORP, pH, NO3 -N, 3 PO 4 -P) were closely monitored over a number of

(b) ORP ORP; ƹPO34 -P;ƶNO3 -N Figure 4 Relation of pH and ORP with phosphorous and nitrate concentration in A/A mode SBR with deficient nitrate for phosphorous uptake üü

The relevant anoxic EBPR processes are phosphorus uptake for polyP formation, glycogen restoring from PHA resources, DPAO growth, lysis and decay. Among them, phosphorus uptake has the highest energy requirement, which is provided by PHA oxidation and thus, results in the highest nitrate consumption (Table 4). In the anoxic phase in SBR4, pH deceases as the nitrate reduction and phosphorous uptake increase. With the denitrification by DPAOs, nitrate is reduced to nitrogen released from the liquid, contributed

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to an increased of pH. Phosphorous uptake by DPAOs also results in an increase of pH until nitrate is completely consumed (Fig. 4). In this case, nitrate is deficient to phosphorous uptake. When nitrate is completely reduced, an anaerobic context occurs, and phosphorous is released again, making pH decrease. Therefore, there is an apex point (point a in Fig. 4) in pH profile, which coincides with the end of phosphorous uptake. The ORP value decreases during the denitrification followed by consumption of nitrate during the anoxic phase. With depletion of nitrate, a minimum value of ORP is observed, and designated as the knee point of nitrate (point b in Fig. 4). This point also indicates the end of denitrification and conversion of nitrate, which is usually used as inflection points to control anoxic phase in nitrogen removal SBR [13, 16, 17, 2124]. In the case of deficient nitrate for phosphorous uptake, the knee point in ORP profile can be detected and used to terminate the anoxic phase. 3.2.2 Sufficient nitrate for phosphorous uptake The typical track analysis in the case of sufficient nitrate for phosphorous uptake is shown in Fig. 5. In

the anaerobic phase phosphorous release takes place substantially companied by continuous decrease of ORP and pH, same as the results for the case of deficient nitrate. In subsequent anoxic phase, with the introduction of nitrate phosphorous uptake initiates. With a sufficient nitrate supply, phosphorous uptake ends prior to the depletion of nitrate. The rise in anoxic pH is due to the denitrification and phosphorous uptake by DPAOs. However, there may be other heterotrophic bacteria responsible for the denitrification with CO2 production. The continuous accumulation of CO2 results in a decrease of pH. Therefore, when phosphorous uptake rate becomes slow in 320 min, the decrease in pH profile is obvious until the end of phosphorous uptake. Utilizing the surplus nitrate heterotrophic denitrifier reduces nitrate, causing the rise in the pH. Therefore, the infection point (point a in Fig. 5) indicates the end of phosphorous uptake. Anoxic ORP profile is similar to that in the case of deficient nitrate. However, the knee point (point b in Fig. 5) is corresponding to the depletion of nitrate rather than the end of phosphorous uptake. Therefore, the pH profile is reliable to provide the information on phosphorous dynamics, while the knee point in anoxic ORP profile is to detect the end of nitrate completion. 4

3

ƸPO 4

(a) pH -P;ƺNO3 -N; üü pH

CONCLUSIONS

This paper presents the on-line control method for the timing of anaerobic, aerobic and anoxic phase in EBPR SBR. The pH and ORP are used as the indirect process indicators. Three systems with either PAOs or GAOs as dominant species are investigated by feeding glucose as main carbon source and changing P/C ratio in influent, which are beneficial to PAOs or GAOs. Continuous measurements of pH and ORP are related to the dynamic behavior of anaerobic phosphorus release and aerobic/anoxic phosphorus uptake in the EBPR SBR. The time evolution of these parameters clearly indicates the end of anaerobic phosphorus release and aerobic/anoxic phosphorus uptake, providing information on the state of process for determining the operating time required for each phase or a cycle. For different bacteria community, pH profiles in the anaerobic phase are different, so that it can be used to identify the community structure. An on-line information and diagnosis system is developed to detect pH deviations in the anaerobic phase for prediction of possible abnormal states in EBPR community structure. NOMENCLATURE

(b) ORP 3  üü ORP; ƸPO 4 -P;ƺNO3 -N Figure 5 Relation of pH and ORP with phosphorous and nitrate concentration in A/A mode SBR with sufficient nitrate for phosphorous uptake

A/A A/O DO DPAO EBPR GAO MLSS

anaerobic-anoxic cycle anaerobic-aerobic cycle dissolved oxygen denitrifying PAO enhanced biological phosphorus removal glycogen accumulating organism mixed liquor suspended solids

Chin. J. Chem. Eng., Vol. 17, No. 3, June 2009 MUCT ORP PAO P/C PHA SBR VFA WWTP

modified University of Cape Town oxidation-reduction potential phosphorous accumulating organism ratio of phosphorous to organic concentration (COD) polyhydroxyalkanoate sequencing batch reactor volatile fatty acid wastewater treatment plant

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