US20160257589A1

US20160257589A1 - Method and apparatus for nitrogen removal in wastewater

Info

Publication number: US20160257589A1
Application number: US15/150,842
Authority: US
Inventors: Bernhard Wett; Ahmed Omari; Pusker Regmi; Mark Miller; Charles B. Bott; Sudhir N. Murthy
Original assignee: DC Water and Sewer Authority; Hampton Roads Sanitation District
Current assignee: DC Water and Sewer Authority; Hampton Roads Sanitation District
Priority date: 2012-09-13
Filing date: 2016-05-10
Publication date: 2016-09-08
Also published as: US9340439B2; US20140069863A1

Abstract

A reactor and control method thereof for nitrogen removal in wastewater treatment achieves a measured control of maintaining high ammonia oxidizing bacteria (AOB) oxidation rates while achieving nitrite oxidizing bacteria (NOB) repression, using various control strategies, including: 1) ammonia and the use of ammonia setpoints, 2) operational DO and the proper use of DO setpoints, 3) bioaugmentation of a lighter flocculant AOB fraction, and 4) proper implementation of transient anoxia within a wide range of reactor configurations and operating conditions.

Description

This application claims the benefit of U.S. Provisional Application No. 61/700,717, filed Sep. 13, 2012. The entire disclosure of U.S. Provisional Application No. 61/700,717 is incorporated herein by reference.

BACKGROUND

The inhibition of nitrite oxidizing bacteria (NOB) is a precondition for the implementation of short-cut biological nitrogen removal (ScBNR) processes such as nitritation-denitritation (Ciudad et al., 2005; Gee and Kim, 2004; Ju et al., 2007; Yoo et al., 1999; Yu et al., 2000; Zeng et al., 2008), nitrite-shunt and partial nitritation-anammox (Fux et al., 2002; Hippen et al., 1997; van Dongen et al., 2001; Wett, 2006; Wen, 2007; Wett et al., 2010), and deammonification. Successful repression of nitrite oxidation by controlling NOB saves 25% oxygen and 40% organic carbon compared to conventional nitrification-denitrification (Turk and Mavinic, 1986; Abeling and Seyfried, 1992). In deammonification processes, the control of NOB results in added benefits in further reductions in aeration energy required, and reduced costs of electron donor and solids handling. FIG. 1, FIG. 2 and FIG. 3 show flowcharts for nitrogen removal through conventional nitrification/denitrification, nitritation/denitritation and deammonification (partial nitritation+anaerobic ammonia oxidation), respectively.
In view of high cost of biological nutrient removal (BNR) to meet increasingly stringent effluent standards, ScBNR through repression of NOB is a topic of interest. Efforts to understand NOB repression have been discussed in many publications, including those that are more specific to the use of high temperature (Hellinga et al., 1998), high levels of free ammonia inhibition, or dissolved oxygen (DO) concentration (Blackburne et al., 2008) and transient anoxia (Kornaros and Dokianakis, 2010). Particularly, all of these conditions are used in part or as a whole, in various approaches, with success in controlling NOB in systems treating ‘high strength’ (high free ammonia) waste streams, such as anaerobic digester dewatering liquor (also usually at high temperature) and landfill leachate. Control of NOB repression in low strength waste streams such as domestic wastewater remains a challenge and is the subject of this invention. The status quo associated with the above features and the controls developed for this invention are described below.
Temperature and Ammonia:
Both temperature and free ammonia are features believed to provide an advantage to ammonia oxidizing bacteria (AOB) over NOB. Free ammonia (FA) inhibition of NOB has been well-documented in literature ever since it was considered by Anthonisen et al. (1976). However, knowledge of controlling FA inhibition to obtain stable nitritation is more limited since NOB adaptation has been reported (Turk and Mavinic, 1989; Wong-Chong and Loehr, 1978). Further, high temperature is known to favor growth of AOB over NOB (Kim et al., 2008).
The increased activity of AOB compared to NOB at higher temperature, greater disassociation of total ammonia to free ammonia and resulting NOB inhibition at higher temperatures, combined with low DO operation (often conducted using intermittent aeration and with managed aerobic solids retention time (SRT)), results in enrichment of AOB and selective wash out of NOB. These approaches are variously described (EP 0826639 A1, EP 0872451 B1, US 2010/0233777 A1, U.S. Pat. No. 7,846,334 B2, U.S. Pat. No. 6,485,646 B1, WO 2012/052443 A1) to control NOB in ‘high strength’ wastewater. These methods either use suspended growth (WO 2006/129132 A1), attached growth on the support media (US 2011/0253625 A1, EP 0931768 B1) or granular sludge (Wett, 2007; U.S. Pat. No. 7,846,334 B2) to accomplish ScBNR.
In spite of being effective, the role of elevated temperature to increase activity of AOB and for the control of NOB growth is not feasible in low strength mainstream processes operating under wide range of temperatures. Consequently, NOB control in low strength wastewater remains intractable and requires careful manipulation of factors other than temperature or free ammonia.
Dissolved Oxygen:
Dissolved oxygen (DO) can play a significant role in control of NOB in low strength wastewater. Sustained nitritation with the use of low DO concentration has been observed in a variety of reactor configurations (Slickers et al., 2005; Wyffels et al., 2004; Blackburne et al., 2008). Although, all of these reports lack account of underlying mechanisms, they resort to a hypothesis of higher oxygen affinity of AOB compared to the NOB (Hanaki et al., 1990; Laanbroek and Gerards, 1993; Bernet et al., 2001) as an explanation for the observed phenomenon (Yoo et al., 1999; Peng et al., 2007; Lemaire et al., 2008; Gao et al., 2009; Zeng et al., 2009). Although the hypothesis that low-DO operation favors AOB versus NOB is very widespread (see review of oxygen half-saturation parameters in Sin et al., 2008) some research results point in the opposite direction (Daebel et al., 2007; Manser et al., 2005) and also inventors' data (see FIG. 4 and FIG. 5) indicates stronger adaptation to low DO-concentration for NOB compared to AOB.
Bioaugmentation:
The transfer of nitrifying biomass from a high strength reactor to the low strength mainstream reactor, such that the SRT required to perform nitrification is decreased in the mainstream process has been reported before (U.S. Pat. No. 7,404,897 B2, U.S. Pat. No. 6,602,417 B1). This bioaugmentation can occur from a separate sidestream reactor or a reactor co joined with the mainstream reactor (Parker and Wanner, 2007). There is also existing prior art related to the physical separation of a more dense biomass fraction containing predominantly anammox organisms and recycling this heavier fraction by the use of the hydrocyclone in order to enrich this very slowly growing biomass (EP 216352481, US 2011/0198284 A1).
Transient Anoxia:
The use of transient anoxia has been a common approach to achieve NOB repression (Li et al., 2012; Ling, 2009; Pollice et al., 2002; Rosenwinkel et al., 2005; Zekker et al., 2012; U.S. Pat. No. 7,846,334 B2; EP 0872451 B1; WO 2006/129132 A1). Transient anoxia allows for a measured approach to control the aerobic SRT as well as to introduce a lag-time for NOB to transition from the anoxic to aerobic environment. Kornaros and Dokianakis (2010) showed delay in NOB recovery and NOB lag adaptation in aerobic conditions following transient anoxia, thus confirming the observations of the usefulness of transient anoxia by many others (Allenman and Irvine, 1980; Katsogiannis et al., 2003; Sedlak, 1991; Silverstein and Schroeder, 1983; Yang and Yang, 2011; Yoo et al., 1999). Although transient anoxia has been used successfully to control NOB in ‘high strength’ wastes (Wett, 2007; U.S. Pat. No. 7,846,334 B2) and the ability to use it in low strength wastes has been suggested (Peng et al., 2004), the ability to control the features associated with transient anoxia remains an enigma until this invention.
To summarize, there exists a need for clear control strategies that exploit the underlying mechanisms of maintaining high AOB oxidation rates while achieving NOB repression with 1) ammonia and the use of ammonia setpoints, 2) operational DO and the proper use of DO setpoints, 3) bioaugmentation of a lighter flocculant AOB fraction, and 4) proper implementation of transient anoxia within a wide range of apparatus (reactor configurations) and operating conditions.

SUMMARY OF THE INVENTION

The claimed invention achieves a proper and measured control of maintaining high AOB oxidation rates while achieving NOB repression, using various control strategies, including: 1) ammonia and the use of ammonia setpoints, 2) operational DO and the proper use of DO setpoints, 3) bioaugmentation of a lighter flocculant AOB fraction, and 4) proper implementation of transient anoxia within a wide range of apparatus (reactor configurations) and operating conditions.

BRIEF DESCRIPTION OF THE DRAWINGS

FIG. 1 is a molar flowchart showing the reactions associated with conventional nitrification and denitrification.

FIG. 2 is a molar flowchart showing the reactions associated with nitritation and denitritation.

FIG. 3 is a molar flowchart showing reactions associated with deammonification.

FIG. 4 is a line graph comparing collected data of KO-values of total nitrifiers (AOB+NOB) and NOB only in bench-scale batch-reactors at Blue Plains Waste Water Treatment Plant (WWTP) (left) and in full-scale at Strass WWTP (right).

FIG. 5 is a graph (left) showing plotted test data of specific nitrogen process rates in terms of ammonia removal per g VSS and day depending on the DO-setpoint of the intermittent aeration of the batch reactors; Monod expressions (right) are fitted to the measured data by applying least square error minimization (the arrow indicates 15% higher N-processing rates of AOB at a DO-level of 1.5 mg/L).

FIG. 6 is a temporal graph comparison of DO depletion curves between two identical SBRs operated with the same aeration regime, one being fed with primary treated effluent (PE) and the other with secondary treated effluent (SE). Note the higher chemical oxygen demand (COD) in the PE fed system allow for more rapid transitions to anoxia from high DO setting.

FIG. 7 is a flowchart showing a DO control algorithm based on ammonia and DO concentrations.

FIG. 8 is a comparison graph showing an illustration of implementation of transient anoxia logic with representative setpoints and control parameters.

FIG. 9 is a graph comparing ammonia oxidation rates and nitrite oxidation rates in a reactor operated under strategy described in Plug Flow and completely mixed Process (Aeration Time Control).

FIG. 10 is a graph comparing Nitrogen species (NH₃, NO₂and NO₃) profiles during reaction phase in SBR configuration operated with intermittent aeration [residual ammonia].

FIG. 11 is a graph comparing Nitrogen species (NH₃, NO₂and NO₃) profiles during reaction phase in SBR configuration operated with intermittent aeration [no residual ammonia].

FIG. 12 is a lateral cross-sectional view of a BNR reactor fitted with mechanical mixer, air diffuser, ammonia and DO sensors.

FIG. 13 is a chart showing a plug flow reactor configuration for ScBNR operation using space based aeration control. [AeZ=aerobic zone; AnZ=anaerobic zone; SZ=swing zone].

FIG. 14 is a graph showing SBR aeration control for intermittent aeration configuration. [The numerical values in this figure are specific to this particular aeration scenario and are not to be used as general recommendation].

DETAILED DESCRIPTION

The present invention develops approaches to increase AOB oxidation rates and to repress and control NOB through ammonia, DO, bioaugmentation and transient anoxia control. The proposed inventions associated with these four features (as compared to the status quo previously described) and the controls developed for this invention are described below.
Temperature and Ammonia:
The current invention shifts away from the more typical use of temperature and free ammonia to achieve NOB repression. The use of temperature to control relative growth rates of AOB and NOB is not always possible within mainstream processes. It is proposed by the inventors that a control feature can be developed that uses the direct measurement of ammonia itself as a controlling variable instead of free ammonia and temperature. The invention uses direct control of the extent of ammonia oxidation, such that ammonia is oxidized throughout a specified reactor time cycle or a specific reactor length. Allowing residual ammonia will maintain pressure on NOB by maintaining high AOB rates.
Dissolved Oxygen:
While the papers discussed in the background section proposed the differences in affinities (e.g., stronger adaptation to low DO-concentration for NOB compared to AOB), the opportunities to employ these differences in a control scheme were discovered by the present inventors. Thus surprisingly and contrary to previous interpretations, transiently high DO operation appears more appropriate to out-compete NOB. The case for using higher DO levels is a differentiator in this invention from the prior art. The higher DO not only maintains high AOB rates, but also manages the relative substrate affinities of AOB and NOB towards NOB repression.
Bioaugmentation:
Different from the prior art approach discussed in the background section, which aims to select the heavier biomass fraction, the current invention aims to select the lighter biomass fraction (e.g., the overflow instead of the underflow of the hydrocyclone) containing predominantly AOB, in order to bioaugment the relatively fast growing AOB from the sidestream reactor to the mainstream, without uncontrolled loss of anammox activity in the sidestream reactor. The selection of the lighter biomass fraction using a cyclone, or sieve, or the unattached biomass separated from a biofilm carrier media in the case of a moving bed biofilm reactor (MBBR) or integrated fixed-film activated sludge (IFAS) reactor, allows a maximum seeding rate which helps to repress NOB in both the high-strength reactor (selectively decreasing SRT) and the low-strength system (transfer of AOB but almost no NOB).
Transient Anoxia:
The case for rapid transition from a high DO into anoxia is another subject of this invention. Rapid transitions to anoxia not only allow little space for NOB to grow, rapid transitions from anoxia back to a high DO set point also allow for the inhibition of the growth of NOB. The transition from anoxia can also produce intermediates that are inhibitory to NOB. It is by nature that nitrite oxidation follows ammonia oxidation. Most models use a substrate half saturation based on the Monod equation (Monod, 1949) to describe the ability to use both the electron donor and acceptor. In a rapidly changing DO environment, some nitrite is likely to accumulate towards the end of ammonia oxidation based on substrate half saturation associated with NOB and the need for available nitrite prior to substantial NOB metabolism. In that situation, if the aeration is continued, the residual nitrite will eventually be converted to nitrate by NOB; however, if aeration is discontinued and the conditions are allowed to rapidly transition to anoxia, the remaining nitrite will be ‘anoxically’ reduced by either chemical oxygen demand (COD) driven heterotrophic denitrifiers in nitrite-shunt processes or by anammox in a single stage deammonification processes. Hence, nitrite-reducing bacteria (e.g., heterotrophic denitrifiers or anammox) may out-compete the NOB (by consuming nitrite), thereby creating pressure on NOB by limiting the availability of their substrate. The NOB population will gain less and less energy in every subsequent cycle, further reducing the active population thereof. Therefore, it is critical to restrict aeration and to rapidly transition to anoxia at the end of ammonia oxidation such that NOB are deprived of DO when nitrite is available.
In the invention, rapid transitions to anoxia are allowed for by maintaining higher oxygen uptake rates through an increase in mixed liquor solids concentration, or by introducing COD in the anoxic phase to rapidly scavenge oxygen. FIG. 6 shows an example of this comparing the DO profiles for two SBR systems operated in intermittent aeration mode where one was fed a primary treated effluent and the other was fed secondary treated effluent. Second, the invention directly measures ammonia in concert with a DO and Anoxic(A)-Oxic(O) hydraulic residence time (HRT) control algorithm (see FIG. 7) to achieve a rapidly alternating aerobic and anoxic environment (FIG. 8). Under this strategy, the ammonia is measured and maintained either within certain predetermined ammonia set points or at a single setpoint with appropriate bandwidth, which depends on the hydraulic regime of the reactor. This approach eliminates the concern of over-aerating after the near completion of ammonia oxidation as residual ammonia is always maintained, which further helps to maintain high AOB rates. Hence, the invention is capable of exploiting known NOB repression strategies with use of a robust control algorithm based on direct ammonia and DO signals. FIG. 9 and FIG. 10 demonstrate the performance of this strategy in controlling NOB to achieve ScBNR in a nitrite-shunt system and single stage deammonification system, respectively. FIG. 11 illustrates the negative impact of over aerating (indicated by no residual ammonia) on NOB repression (indicated by nitrate production).
Specific controls for controlling NOB through these four features (ammonia, DO, bioaugmentation and transient anoxia control) are now described.
Dissolved Oxygen Setpoint Control:
It is desirable to maintain a dissolved oxygen (DO) setpoint as much above 1 mg/L as practicable. A higher DO setpoint allows for a more rapid growth of AOB over NOB. However, a very high DO setpoint increases the time-to-transition to anoxia. One approach that has been successfully used for achieving this high DO strategy is described in the control narrative below. It should be noted that this high DO strategy is in opposition to the conventional wisdom of achieving nitrite shunt for low strength and to the actual practice of achieving nitrite shunt in high strength and high temperature waste streams.
Ammonia Setpoint Control:
The aerobic SRT is controlled through two approaches. An increase in solids wasted decreases the total and aerobic SRT. A second approach to decreasing the aerobic SRT is by increasing the anoxic time step during transient anoxia. In an intermittently aerated (in time or space) BNR reactor operated under ammonia-based DO control (in time)/A-O HRT control (in space) strategy, aerobic SRT is determined by aeration needs of AOB to oxidize ammonia to meet the imposed ammonia set points. For example, if AOB's ammonia oxidation rate is lower, more aeration will be required to meet the same ammonia set point compared to when AOB rates are higher. In such a scenario, intentional lowering of the total SRT gradually results in a reduction in AOB ammonia oxidation rate at a certain DO value. Consequently, AOB require more aeration to increase their growth rate and to meet the desired ammonia set point, causing the operational high DO set point (in case of ammonia-based DO control) and aerobic HRT (in case of ammonia-based A-O HRT control) to increase and be at a point where the growth of AOB are favored over NOB.
Current systems that attempt to achieve nitrite shunt do not operate at aggressive aerobic SRTs and therefore are unable to achieve suitable conditions for NOB repression. The invention's desire for operating at a high DO setpoint allows for a more aggressive SRT operation strategy, which while maintaining high AOB oxidation rates, supplies additional pressure for NOB repression. The bioaugmentation of AOB from a sidestream reactor or an upstream stage will allow aerobic SRT to be even lower, which can cause selective wash out of NOB. In addition, the application of aggressive SRT pressure is easily controlled in this invention. Since the ammonium setpoint determines the operational high DO setpoint (in case of ammonia-based DO control) and aerated fraction (in case of ammonia-based A-O HRT control), our work has suggested that it is a simple matter to control the total SRT such that the DO remains at a high concentration, in excess of 1 mg/L.
Bioaugmentation:
Bioaugmentation of AOB from a sidestream process via a selection device to the mainstream results in enrichment of AOB and allows aggressive control of SRT to washout NOB while meeting ammonia oxidation needs. In a similar manner, bioaugmentation of anammox organisms via a selection device from a sidestream or high strength reactor is also possible.
Transition to Anoxia Control:
A more rapid transition between aerobic setpoint and anoxia is desirable to minimize the time available for NOB to grow favorably over AOB. There are at least three approaches to increase the oxygen uptake rates to transition to anoxia. One approach is to operate the reactor at higher mixed liquor solids concentration, such that there are more organisms seeking air in the same volume (low hydraulic residence time). Another approach is to use influent COD to allow for the scavenging of oxygen during the transition periods. A third approach is to increase the temperature and thus the growth rates of all organisms. The key feature is to allow for high oxygen uptake rates to transition from oxic to anoxic conditions.
Transient Anoxia Frequency (TAF) Control:
It is desirable to have a high TAF to allow for rapid changes between aerobic and anoxic conditions while maintaining the same overall aerobic SRT. For example a 5 minute aerobic/anoxic cycle is preferred over a 15 minute aerobic/anoxic cycle, which is preferred over a 30 minute aerobic/anoxic cycle. A highest practicable TAF allows for disruption of NOB while allowing for preferential growth of AOB in the aerobic phase and denitrifying organisms or anammox organisms in the anoxic phase. There are constraints to maximizing this frequency. The increase in frequency, maximum value, is eventually constrained in the aerobic step by the time required to allow oxygen to achieve its setpoint and then to sufficiently oxidize ammonia. Additionally, a minimum anoxic time is required to allow denitrifying or anammox organisms to convert nitrite to nitrogen gas.
Reactor Configurations:
Several apparatus are available to execute this AOB oxidation and NOB repression framework, including complete mixed reactors, sequencing batch reactors, oxidation ditches and plug flow reactors. It should be noted that the reactor apparatus can be adjusted to deliver the control features for achieving SRT, ammonia oxidation requirements, high DO setting and anoxia transitions, where possible, by providing mechanical and hydraulic flexibility for attaining dissolved oxygen settings and anoxic in space or anoxic in time settings. Selectors used to ensure good settling biomass or biological phosphorus removal and swing zones or reactors to accommodate variable flows and loads that are typical to a wastewater treatment process can be provided. In addition to suspended growth reactors, biofilm, granular or hybrids of these reactors are also feasible. Finally, the solid-liquid separation could occur using any separation device including clarifiers, membranes or dissolved air floatation tanks.
Plug flow reactors are characterized as continuously fed reactors with very high length to width ratio and can be simulated as a series of completely mixed reactors where the pollutant concentration decreases along the flow pathway across the reactors length (i.e. concentration gradient). In plug flow continuously fed reactors, which are more commonly used in large treatment plants, the process controls to achieve ScBNR can be addressed using two configurations: (1) controlling aeration in space by alternating between aerobic and anaerobic zones; and (2) controlling aeration in time by cycling air throughout the reactor in “air on” and “air off” sequence similar to SBR configuration. Other features requiring control of mixed liquor and aerobic/anoxic transitions are similar to SBR scheme described above.
Control Strategies
Several control strategies are available that can be applied in the above-mentioned reactor configurations that make use of features of this invention to achieve NOB repression. A few exemplary strategies are described below, optimized for various configurations.
Control Strategy A:
The first control strategy under which the operational DO is variable and controlled by the ammonia concentration in the BNR reactor will optimize the DO for high ammonia oxidation rate. This approach is valid in a wide range of reactor configurations include plug flow, complete mix, complete mix reactors in series, and sequencing batch reactor. Under this approach the DO cycles between the low DO (which is fixed) and a high variable DO, usually greater than 1 mg/L and controlled by reactor ammonia set points. An aggressive aerobic SRT is maintained to increase the demand for oxygen, thus allowing for the controller to automatically increase the DO levels to greater than 1 mg/L. In this control strategy, the aerobic and anoxic periods are dictated by the AOB's aeration requirement to meet ammonia set point, as opposed to being fixed.
In this exemplary embodiment, a BNR reactor may be fitted with DO and ammonia probe (FIG. 12), It will be possible to have any reactor configuration as described in the next subsection where the control can occur either in time or in space. In case of multiple or plug flow reactors, multiple DO probes are installed along each major section along a train, while an ammonia probe will be installed strategically in a latter reactor or section, to manage reaction rates such that small amounts of ammonia residuals are maintained. The aeration in the aerobic reactors is controlled based on the real time NH₄—N concentration in the reactor, which is representative of the effluent NH₄—N. The goal is to achieve certain ammonia set points which could be either single set point, a range between a high and low value, or a small bandwidth. A control scheme is discussed below using high and low ammonia setpoints.
Aeration is regulated by switching an air control valve either ON or OFF, based on a high DO (HDO) and low DO (LDO) setpoint. The LDO setpoint is fixed at near zero (0.001 to 0.1 mg/L) whereas HDO is variable (based on NH₃—N in the tank) from 0.3 mg/L (MinHDO) to 3.0 mg/L (MaxHDO). The MaxHDO is set at 2.5-3.0 mg/L, since adding more aeration beyond this point is believed to provide no added benefit in terms of ammonia oxidation rate, except in the case of MBBR or IFAS reactor where a higher MaxHDO setpoint may be used as a result of dissolved oxygen mass transfer limitations imposed by these processes. When the NH₃—N in tank is greater than the high ammonia-N setpoint (HNH₃—N) (1-4 mg/L), the HDO is increased until the NH₃—N gets below the 1-4 mg/L HNH₃—N setpoint. When the NH3-N concentration is lower than the low ammonia-N setpoint (LNH₃-N) (0.5-2 mg/L), the HDO is decreased until the NH₃—N concentration gets higher than the 0.5-2 mg/L LNH₃-N setpoint (FIG. 7). If the ammonia-N is between the LNH₃-N and HNH₃—N there will be no change in the HDO setpoint. This scenario will be encountered when NH₃—N concentration is going down from the HNH₃—N setpoint or going up from the LNH₃-N setpoint (FIG. 8). A P, PI, or PID controller adjusting the HDO setpoint based on an NH₃—N setpoint with appropriate bandwidth depending on the response time and reactor hydraulics is also possible. Aggressive SRT control is accomplished by wasting solids such that the HDO setpoint is consistently greater than 1 mg/L. The total SRT can also be controlled automatically by maintaining the waste flow rate based on reactor DO concentration over certain averaging time.
Control Strategy B:
To simulate the intermittent aeration control in space (FIG. 13), a reactor is designed such that the entire volume could be mechanically mixed and aerated. Deliberately turning the mixer and aerators either ON or OFF controls the aerobic and anoxic HRT within this reactor. Under a first control strategy, in which the operational DO is fixed at greater than 1 mg/L such that AOB growth is favored over NOB, the DO is maintained at greater than 1 mg/L in the aerated portion of the reactor; however, the aerobic and anoxic fractions within the reactor change to meet the ammonia set point goal. In other words, the aerobic SRT is controlled by the ammonia set point goal, which is achieved by changing aerobic and anoxic HRT through the use of swing zones. The total SRT is controlled aggressively so that at least 50% of the total HRT is aerobic at DO concentration of greater than 1 mg/L. The total SRT can also be controlled automatically by maintaining the waste flow rate based on aerobic HRT over a certain averaging time.
Similar to the aeration control in time, the desired aerobic and anoxic HRTs are achieved in this control method based on a predetermined ammonia set point concentration. If ammonia concentration is greater than the ammonia set point, the aerobic HRT is increased at 4 minute (adjustable) increments, waiting 60 seconds (adjustable) between increases in the aerobic HRT. If ammonia concentration is lower than the ammonia set point, the anoxic HRT is increased at 4 minute (adjustable) increments, waiting 60 seconds (adjustable) between increases in the anoxic HRT.
Control Strategy C:
This strategy entails achieving intermittent aeration in a reactor with the use of predetermined ammonia set points. The reactor is equipped with a mixer and an air diffuser to achieve anoxic mixing and aeration. Under this approach, operational DO is set at greater than 1 mg/L when the reactor is aerated. FIG. 14. illustrates an example of this operation mode in an SBR system. The duration of aeration is controlled based on the high and low ammonia set points. When the ammonia concentration in the reactor is more than the ammonia set point, the reactor will be aerated until the low ammonia set point is reached. As soon as reactor ammonia concentration is lower than the low ammonia set point, reactor aeration is terminated (mixing is provided), such that the ammonia concentration is allowed to fluctuate within this bandwidth with continuously alternating between aerobic and anoxic conditions.

RELEVANT ACRONYMS

AOB: ammonia oxidizing bacteria
AeZ: aerobic zone;
AnZ: anaerobic zone;
BNR: biological nutrient removal
COD: chemical oxygen demand
DO: dissolved oxygen
FA: free ammonia
HDO: high DO
HNH₃—N: high ammonia-N setpoint
HRT: hydraulic residence time
IFAS: integrated fixed-film sludge

LDO: low DO

LNH₃-N: low ammonia-N setpoint
MBBR: moving bed biofilm reactor
NOB: nitrite oxidizing bacteria
OUR: oxygen uptake rate
PE: primary treated effluent
SE: secondary treated effluent
ScBNR: short-cut biological nitrogen removal
SRT: solids retention time
SZ: swing zone

TAF: Transient Anoxia Frequency

WWTP: Waste Water Treatment Plant

DOCUMENTS CITED IN APPLICATION

U.S. Patent Documents

2010/0233777 A1 September 2010 Chandran et al
U.S. Pat. No. 6,485,646 B1 November 2002 Dijkman et al.
2011/0198284 A1 August 2011 Nyhuis
2011/0253625A1 October 2011 Takeda et al.
U.S. Pat. No. 7,846,334 B2 December 2010 Wett
U.S. Pat. No. 6,602,417 B1 August 2003 Zilvertant
U.S. Pat. No. 7,404,897 B2 July 2008 Bailey, Jr. et al.


FOREIGN PATENT DOCUMENTS

EP	0931768B1	September 2003
EP	0826639A1	March 1998
EP	0872451B1	December 2002
EP	216352481	September 2008
WO	2006/129132A1	December 2006
WO	2012/052443A1	April 2012
WO	00370A1	January 1998

OTHER PUBLICATIONS

Abeling and Seyfried (1992) Water Science and Technology 26(5-6): 1007-1015.
Alleman and Irvine (1980) Water Research 14: 1483-1488.
Anthonisen et al. (1976) Journal of Water Pollution Control Federation 48: 835-852.
Bernet et al. (2001) Journal of Environmental Engineering 127: 266-271.
Blackburn et al. (2008) Biodegradation 19(2): 303-312.
Ciudad et al. (2005) Process Biochemistry 40(5): 1715-1719.
Daebel et al. (2007) Water Research 41: 1094-1102.
Fux et al. (2002) Journal Biotechnology 99(3): 295-306.
Gao et al. (2009) Bioresource Technology 100: 2298-2300.
Gee and Kim (2004) Water Science and Technology 49: 47-55.
Hanaki et al. (1990) Water Research 24: 297-302.
Hellinga et al. (1998) Water Science and Technology 37(9): 135-142.
Hippen et al. (1997) Water Science and Technology 35 (10): 111-120.
Ju et al. (2007) Water Environment Research 79(8): 912-920.
Katsogiannis et al. (2003) Water Science and Technology 47(11): 53-59.
Kim et al. (2008) Process Biochemistry 43(2): 154-160.
Kornaros and Dokianakis (2010) Environmental Science and Technology 44: 7245-7253.
Laanbroek and Gerards (1993) Archives of Microbiology 159: 453-459.
Lemaire et al. (2008) Biotechnology and Bioengineering 100(6): 1228-1236.
Li et al. (2012) Process Safety and Environmental Protection. doi:10.1016/j.psep.2012.05.009
Ling (2009) Proceedings of 2nd IWA specialized Conference on nutrient Management in Wastewater treatment Processes pp. 403-410.
Manser et al. (2005) Water Research 39(19): 4633-4642.
Monod (1949) Annual Review of Microbiology 3: 371.
Parker, D. and Wanner, J. (2007) Water Practice 1(5): 1-16
Peng et al. (2004) Water Science and Technology 50(10): 35-43.
Peng et al. (2007) Chinese Journal of Chemical Engineering 15(1): 115-121.
Pollice et al. (2002) Water Research 36(10): 2541-2546.
Sedlak (1991) Phosphorus and Nitrogen Removal from Municipal Wastewater: Principles and Practice (2nd ed.).
Rosenwinkel et al. (2005) Proceedings of IWA specialised Conference on nutrient Management in Wastewater treatment Processes and Recycle streams pp. 483-491.
Silverstein and Schroeder (1983) Journal of Water Pollution Control Federation 55: 377-384.
Sin et al. (2008) Water Science and Technology 58(6): 1155-1171.
Sliekers et al. (2005) Applied Microbial Biotechnology 68: 808-817.
Turk and Mavinic (1989) Water Research 23: 1383-1388.
Turk and Mavinic (1986) Canadian Journal of Civil Engineering 13: 600-605.
van Dongen et al. (2001) Water Science and Technology 44(1): 153-160.
Wett (2006) Water Science and Technology 53(12): 121-128.
Wett (2007) Water Science and Technology 56(7): 81-88.
Wett (2010) Water Science and Technology 61(8): 1915-1922.
Wong-Chong and Loehr (1978) Water Research 12(8): 605-609,
Wyffels et al. (2004) Water Science and Technology 49(5-6): 57-64.
Yang and Yang (2011) Journal of Hazardous Materials 195: 318-323.
Yoo et al. (1999) Water Research 33: 145-154.
Yu et-al. (2000) Journal of Environmental Engineering 126: 943-948.
Zekker et al. (2012) Environmental Technology 33(4-6): 703-710.
Zeng et al. (2008) Chemical Engineering and Technology 31(4): 582-587.
Zeng et al. (2009) Enzyme and Microbial Technology 45(3): 226-232.

Claims

1) A reactor for biological nitrogen removal from wastewaters comprising a nitrite-shunt which targets repression of the nitrite oxidizing bacteria (NOB) under controlled transient anoxia conditions, the conditions being controlled either along the flow-path or along the process time-line, wherein a dissolved oxygen (DO) profile switches between a lower DO-setpoint of less than 0.1 mg/L and a upper DO-setpoint of greater than 1.0 mg/L, and wherein at least one of an aeration system activation interval or the upper DO setpoint are set such that an on-line measured ammonia concentration is higher than an ammonia setpoint of 1.5 mg NH₄—N/L in more than 75% of the transiently aerated reactor volume (in space or time).

2) The reactor of claim 1, wherein said reactor has a limited aerobic sludge retention time just sufficient to reach the ammonia setpoint by controlled extension of anoxic periods or volume and by operating a high sludge wasting rate, wherein the sludge wasting rate is controlled to maintain high DO setpoints (>1 mg/L) in the case of ammonia concentration control of aeration.

3) The reactor of claim 1, wherein said reactor further includes a bioaugmentation of aerobic ammonia oxidizing bacteria (AOB) produced from a high-strength ammonia sidestream reactor, wherein the less dense and more compressible or unattached sludge fraction is selected from the high-strength ammonia sidestream reactor for the bioaugmentation by an appropriate device and fed to the reactor at a maximum rate leading to a retention time of the bioaugmentation fraction of less than 10 days in the sidestream system.

4) The reactor of claim 3, wherein the appropriate device for selecting the biomass for Bioaugmentation from the high-strength ammonia sidestream reactor for the bioaugmentation comprises one of the following devices: a cyclone, centrifuge, lamella settler, sieve, or integrated biofilm process.

5) The reactor of claim 1, wherein said reactor includes a bioaugmentation of anammox organisms from a sidestream reactor to the mainstream reactor in order to provide microbial competitors for nitrite which help to repress NOB.

6) The reactor of claim 1, wherein a mixed liquor solids (MLSS) concentration is higher than 2 g/L, or equivalent biomass quantities in a biofilm system, in order to enhance oxygen uptake rate (OUR) to facilitate rapid transitions from aerobic to anoxic conditions.

7) The reactor of claim 1, further comprising an aeration control system which is configured to maximize the frequency of transitions between aerobic and anoxic conditions.

8) The reactor of claim 1, further comprising an aeration control system which is configured to increase the upper DO-setpoint in correspondence with load increase.

9) The reactor of claim 1, wherein said reactor can be any one of a sequencing batch reactor, a completely mixed reactor, an oxidation ditch or a plug flow process, wherein at least one of the oxic and anoxic steps or DO setpoints is controlled either in time or in space.

10) The reactor of claim 1, wherein said reactor includes one of a suspended growth process, a granular process or a biofilm process or a hybrid combination of these processes.

11) The reactor of claim 1, wherein the separation process can occur using a settler, a dissolved air flotation device, a filter or a membrane.

12) The reactor of claim 1, wherein said reactor maintains a high oxygen uptake rate to allow for a rapid transition to anoxia from an aerated state.

13) The reactor of claim 12, wherein said reactor feeds a minimum mass-flow of organic carbon to the reactor to enhance heterotrophic growth for more rapid transition to anoxia from an aerated state and for additional competition for nitrite for improved NOB-repression.

14) A method of controlling a reactor for biological nitrogen removal from wastewaters comprising a nitrite-shunt which targets repression of the nitrite oxidizing bacteria (NOB) under controlled transient anoxia conditions, the conditions being controlled either along a flow-path or along a process time-line, wherein a dissolved oxygen (DO) profile switches between a lower DO-setpoint of less than 0.1 mg/L and an upper DO-setpoint of greater than 1.0 mg/L, and wherein at least one of an activation of an aeration system of the reactor or the upper DO setpoint is dependent on an on-line measured ammonia concentration being higher than an ammonia setpoint of 1.5 mg NH₄—N/L in more than 75% of transiently aerated reactor volume (in space or time).

15) The method of claim 14, further comprising controlling said reactor to have a limited aerobic sludge retention time just sufficient to reach the ammonia setpoint by controlled extension of anoxic periods or volume and by operating a high sludge wasting rate, wherein the wasting rate is controlled to maintain high DO setpoints (>1 mg/L) in the case of ammonia concentration control of aeration.

16) The method of claim 14, further comprising said reactor receiving a bioaugmentation of aerobic ammonia oxidizing bacteria (AOB) produced from a high-strength ammonia sidestream reactor, wherein the less dense and more compressible or unattached sludge fraction is selected from the high-strength ammonia sidestream reactor for the bioaugmentation by an appropriate device and fed to the main reactor system at a maximum rate leading to a retention time of the bioaugmentation fraction of less than 10 days in the sidestream system.

17) The method of claim 16, wherein the appropriate device is one of a cyclone, centrifuge, lamella settler, sieve, or integrated biofilm process.

18) The method of claim 14, wherein a bioaugmentation of anammox organisms from a sidestream reactor to the mainstream reactor is provided in order to provide microbial competitors for nitrite which help to repress NOB.

19) The method of claim 14, wherein the reactor is controlled to achieve a mixed liquor solids (MLSS) concentration of higher than 2 g/L, or equivalent biomass quantities in a biofilm system, in order to enhance oxygen uptake rate (OUR) to facilitate rapid transitions from aerobic- to anoxic conditions.

20) The method of claim 14, wherein controlling said reactor further comprises controlling an aeration control system to maximize the frequency of transitions between aerobic and anoxic conditions.

21) The method of claim 14, wherein controlling said reactor further comprises controlling an aeration control system to increase the higher DO-setpoint in correspondence with load increase.

22) The method of claim 14, wherein said reactor controlled by the method can be any one of a sequencing batch reactor, a completely mixed reactor, an oxidation ditch or a plug flow process, and wherein at least one of the oxic and anoxic steps or DO setpoints are controlled in time or in space.