April 19, 2018
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Verbyla, M.E. and Rousselot, O. (2018). Membrane Bioreactors. In: J.B. Rose and B. Jiménez-Cisneros (eds), Water and Sanitation for the 21st Century: Health and Microbiological Aspects of Excreta and Wastewater Management (Global Water Pathogen Project). (J.R. Mihelcic and M.E. Verbyla (eds), Part 4: Management Of Risk from Excreta and Wastewater - Section: Sanitation System Technologies, Pathogen Reduction in Sewered System Technologies), Michigan State University, E. Lansing, MI, UNESCO. https://doi.org/10.14321/waterpathogens.63
|Last published: April 19, 2018|
Membrane bioreactors (MBRs) are a sanitation technology used in centralized wastewater treatment facilities and, infrequently, in some onsite systems. They are similar to activated sludge systems, but utilize micro- or ultra-filtration membranes instead of secondary clarifiers to remove bacterial biomass from secondary wastewater. Some pathogen reduction is achieved in MBRs during biological treatment, but a much greater reduction is achieved as the mixed liquor passes through the membrane. The pore sizes of membranes typically used in these systems will retain most bacteria, but are large enough for viruses to pass through. However, the smaller effective pore sizes due to the development of a cake layer considerably increase the efficiency of virus removal in these systems. Under normal operating conditions, on average, these systems achieve 4.4-log10 reduction of bacterial pathogens and 3.3-log10 reduction of viral pathogens. Some of the most important factors influencing pathogen reduction efficiency in MBRs include the ratio of pathogen size to membrane pore size, the extent of membrane fouling, variations in feed water, membrane integrity, solids retention time and hydraulic retention time. The efficiency of pathogen reduction in MBR systems will also undoubtedly be influenced by local conditions, including socioeconomic and geographical factors that affect a community’s ability to provide proper maintenance to these systems. MBR is a complex treatment process that should be intensively validated before assigning log10 reduction credits. Any log10 reduction values reported herein should require local validation prior to being used for regulatory purposes. Additionally, the sludge wasted from MBR systems likely contains high concentrations of pathogens, although this has not been well studied. MBR sludge should be treated to further reduce pathogens prior to reuse or disposal.
Membrane bioreactors (MBR) are a sanitation technology generally used in centralized wastewater treatment facilities, and variations of this technology are also used in onsite systems as retrofits or modifications to conventional septic systems (Chiemchaisri et al., 1993) (Figure 1). An MBR system is a modification of activated sludge, with micro- or ultra-filtration membranes used instead of secondary clarifiers to remove bacterial biomass from the treated effluent. MBR systems may have membranes that are external (located outside the aeration tank) or immersed (located inside the aeration tank). These systems commonly operate with solids retention times of 20 to 30 days and hydraulic retention times of 6 to 10 hours. Membranes can be made from mineral or organic materials, and typically have tubular, hollow fiber, or plate-like shapes. Wastewater is passed through the membrane under vacuum conditions or using hydrostatic pressure. Figure 2 shows a schematic of a wastewater treatment system in France that utilizes the MBR technology.
Figure 2. Schematic of an MBR system with an external membrane, based on the Seine Morée Wastewater Treatment Plant in France, which is operated by the Conurbation of Paris Sanitation Authority (SIAAP), and serves a population of 300,000 residents. The plant uses the ULTRAFOR® membrane bioreactor process with ZeeWeed 500 hollow fiber membranes (see photo inset), which have a cut-off threshold of 0.04 µm. Approximately 62% of flow from the membrane gets recirculated back to the aerobic chamber, while 18% of flow from the aerobic chamber recirculates to the anoxic chamber, and 16% of flow from the anoxic chamber circulates back to the anaerobic chamber. (photo credits SIAAP-DDP).
MBRs are typically used to treat wastewater from domestic sources, or from a mixture of domestic and industrial sources. Figure 3 shows the typical input and output of a MBR system. The influent to the membrane of an MBR system may have already passed through a primary clarifier, often followed by sieving or fine screening, and then some secondary treatment in the activated sludge aeration tank. Therefore, the concentrations of pathogens entering the membrane may be slightly lower than they were in the untreated wastewater. However, pathogens in the return activated sludge can actually cause the concentration at the influent of the membrane to be greater than the concentration in the untreated wastewater (Simmons et al., 2011). Typical concentrations for pathogens in the liquid and/or solid inputs to MBR systems are provided in the Introduction.
The outputs from MBR systems include treated water effluent and sludge. The treated effluent is continuously discharged. The sludge, generated from the process of membrane fouling, accumulates over time and is typically removed every few weeks. This sludge is often mixed with sludge from the primary clarifier, and must be treated prior to reuse or land application (see Chapter on Sludge Management). MBR systems with anaerobic units can also produce biogas that can be harvested and reused for energy production.
Figure 3. Typical inputs and outputs from membrane bioreactor systems.
MBR systems usually include primary treatment, and some pathogen reduction is achieved in primary clarifiers where larger pathogens and pathogens associated with larger particles settle out of the wastewater and are transferred to the primary sludge (see chapters on Preliminary Treatment and Primary Sedimentation). After primary treatment, pathogen concentrations in MBR systems are reduced by a combination of inactivation (loss of viability) and removal (retention in the sludge) (Tables 1a and 1b). Predation is the main mechanisms of pathogen reduction during biological treatment, and size exclusion is the main mechanism of pathogen reduction by the membrane. The efficiency of pathogen reduction via predation during biological treatment is 4 to 7 log10 units lower than the reduction achieved via size exclusion by the membrane (Branch et al., 2016a). However, activated sludge flocs are also formed during biological treatment, and the presence of pathogens attached to or enmeshed within these flocs also affects how well they are removed by the membrane (Hai et al., 2014).
Just like in conventional activated sludge systems, pathogens are reduced during biological treatment process in MBR systems. This reduction is primarily attributed to natural decay, predation by organisms of higher trophic levels, and the production of proteolytic enzymes by the consortia of microorganisms in the mixed liquor (Kim and Unno 1996; Hao et al. 2010; Sidhu et al. 2015). See the Activated Sludge chapter for more details about the factors affecting pathogens during biological treatment.
Greater adsorption of pathogens to suspended solids leads to more efficient removal at the membrane (see Section 3.2). There are several factors related to the influent water quality that can affect adsorption of pathogens to mixed liquor suspended solids, such as the concentration and composition of organic matter, salt content, pH, ambient temperature, and bacterial density (Stevik et al., 2004). Design and operational factors such as longer hydraulic retention times (George et al., 2002) and the use of alternating anoxic/oxic reactors, as in the Bardenpho process (Schmitz et al., 2016), can also improve pathogen removal efficiency.
Chaudhry et al. (2015a) estimated that virus decay due to predation and enzymatic activity alone was responsible for 1.1 to 1.7 log10 of the overall 5.5 to 7.1 log10 removal in a full-scale MBR system with a pore size of 0.04 µm. Likewise, Branch et al. (2016a) reported negligible to 0.9 log10 unit reduction of FRNA and somatic coliphages during biological treatment, with an additional 3.2 to 4.4 log10 unit reduction provided as the mixed liquor passed through the membrane. The same authors reported <1.1 log10 unit reductions of E. coli (rod-shaped bacteria, 1-2 mm long, 0.25-0.5 mm wide) during biological treatment, but an additional 4.7 to 6.7 log10 unit reduction of E. coli as the mixed liquor passed through the membrane. The concentration of Clostridium perfringens spores actually showed an apparent increase in concentration during biological treatment (Branch et al., 2016a), but were consistently reduced at the membrane by more than 6 log10 units.
The primary mechanism for pathogen removal as the mixed liquor passes through the membrane is size exclusion, which is enhanced by the development of the biological cake layer that develops on the mixed liquor side of the membrane (Chaudhry et al., 2015a; Chaudhry et al., 2015b). Some pathogens retained by the membrane or cake layer may also lose viability due to predation or the production of proteases or nucleases by other microorganisms in the biofilm (Bosch et al., 2006; Chaudhry et al., 2015a). It should be noted, however, that in other settings, biofilms have been shown to offer protection to some bacterial pathogens (e.g. V. cholerae) from predation by larger microorganisms (Matz et al., 2005). It should be assumed that most of the pathogens retained at the membrane will be transferred to the secondary sludge where they may remain viable and must be further treated (see Sludge Management chapter). In general, the viability of pathogens recovered in full-scale MBR system secondary sludge has not been well studied.
Figure 4. Major factors affecting pathogen removal in membrane bioreactors.
The pore sizes of most membranes used in practice are not small enough to physically remove viral pathogens by size exclusion alone; most MBR systems in practice employ microfiltration (0.1- to 0.4-µm nominal pore size) or ultrafiltration (nominal pore size of 0.01- to 0.04-mm) (Hai et al., 2014). However, membranes in MBR systems with larger pore sizes have still been shown to reduce the concentration of viruses by 3 to 4 log10 units, due to the smaller effective pore sizes and adsorption in cake layer (Lv et al., 2006; Chaudhry et al., 2015a). Chaudhry et al. (2015a) reported an overall removal of 5.5 log10, 5.6 log10, and 7.1 log10 for adenovirus (measured via qPCR), norovirus GII (measured via RT-qPCR), and F+ coliphage (measured via plaque assay), respectively, in a full-scale MBR system after a 4- to 5-day cake layer was developed. The authors determined that the development of the cake layer was responsible for a 1.6 log10 increase in the removal of adenovirus and F+ coliphage, and a 0.4 log10 increase in the removal of norovirus GII. As such, virus removal efficiency in MBR systems may decrease immediately after the membranes are cleansed or treated for routine operation and maintenance (Lv et al., 2006).
Membranes have a distribution of pore sizes—the nominal pore size typically refers to a filter that is capable of cutting off a certain percentage by weight (e.g. 90%) of glass beads with diameters greater than the specified size. Therefore, a small percentage of pores on the membrane will be larger than the nominal pore size, which explains the fact that pathogens larger than the nominal membrane pore size are sometimes detected on the downstream side of the membrane. It should also be noted that some bacteria may undergo deformation mechanisms, allowing them to pass through membranes with pore sizes smaller than the cell size (Gaveau et al. 2017). Differences in the thickness and elasticity of the cell wall enable Gram negative bacteria to have greater deformability than Gram positive bacteria. Figure 5 shows the log10 reduction of viruses and fecal indicator bacteria in MBRs with respect to the ratio of the size of the microorganism to the nominal pore size of the membrane. For ratios greater than 1, the log10 removal increases as the ratio increases. However, for ratios below 1 (i.e. viruses that are smaller than the nominal pore size of the membrane), the removal is not correlated with this ratio, and likely depends on other factors such as the development of the gel and cake layers and the transmembrane pressure.
Figure 5. Virus and fecal indicator bacteria removal efficiency in membrane bioreactors with respect to the ratio of microorganism size to nominal pore size of the membrane (data sources: Branch et al., 2016b; Chaudhry et al., 2015a; Chaudhry et al., 2015b; Francy et al., 2012; Hai et al., 2014; Kuo et al., 2010; Lv et al., 2006; Marti et al., 2011; Purnell et al., 2016; Shang et al., 2005; Simmons et al., 2011; Wu et al., 2010; Zanetti et al., 2010; Zhang and Farahbakhsh 2007; Zheng and Liu, 2006).
Table 2 includes a summary of the key factors that affect pathogen removal in MBR systems. Some of the most critical design and operational factors, maintenance issues, and malfunction concerns that will affect pathogen removal efficiency in MBR systems:
Membrane Pore Size and Pathogen Size. The nominal pore size of the membrane impacts the efficiency of pathogen removal for MBRs. Pathogen removal becomes more efficient and consistent when the ratio of the diameter of the pathogen to the nominal pore size of the membrane is 2.0 or higher (Figure 5).
Membrane Fouling. Membrane fouling is the most challenging issue in the operation of MBRs (Meng et al., 2017) and it generally (but not always) increases pathogen reduction efficiency in ways that are not yet fully understood. This is because fouling itself is a very complicated issue that is still not yet fully understood and is an active topic of current research (Wang et al., 2014; Meng et al., 2017). An increase in the transmembrane pressure or a decrease in the flux across the membrane is an indication of membrane fouling. Increased virus removal efficiencies have been reported at higher transmembrane pressures in bench-scale systems operating under constant flux (Zanetti et al., 2010; Marti et al., 2011; Yin et al., 2016). However, Yin et al. (2015) reported that the level of fouling alone is not a good predictor for virus removal, and that pore blockage by dissolved species increases virus removal but the cake layer may either increase or decrease virus removal efficiency depending on its properties.
After a fouled membrane is cleaned, pathogen (especially virus) removal efficiency may be temporarily lower than normal, until a cake layer has been sufficiently developed (Chaudhry et al., 2015a), which may take several days or weeks. Branch et al. (2016a) reported that virus removal decreased slightly but became more consistent after the replacement of 10-year-old fouled membranes; they also reported that the removal of E. coli and C. perfringens increased after the membranes were replaced. Yin et al. (2016) reported that after using pressure relaxation and backwashing to control fouling, the membrane permeability increased and the removal of adenovirus decreased by as much as 0.8 log10 units; they also reported that the backwash flux had the greatest influence on changes in virus removal efficiency, not the duration of the backwash.
Feed Water Variations. Branch et al. (2016b) studied the effects of feed water variation and process failures on the efficiency of the reductions of virus, protozoa and bacteria indicator organisms (FRNA phage, C. perfringens, and E. coli, respectively). They found that short-term COD loading of 5 g/L temporarily increased virus removal to >6.9 log10 units (presumably due to a pH drop), short-term NH3 loading of 0.7 g/L temporarily reduced virus removal to 4.4 log10 units, and salinity shock of 20 g/L NaCl temporarily reduced virus removal to 3.9 log10 units. For each of these three feed water variation cases, virus removal efficiencies recovered or returned to normal within 2 – 3 days after the shock loading event. To address the potential issues of feed water variation, equalization tanks can be used to normalize the quality of feed water, and pretreatment standards for industrial entities can be enforced.
Process Failures and Membrane Integrity. Over time, membranes may lose their integrity by experiencing physical damage, pore sizes that are larger than normal, or compromised O-rings or glue lines. Some common reasons for the loss of membrane integrity include manufacturing defects, the use of incompatible chemicals for cleaning, violation of the manufacturer’s maximum recommended operating pressure, or damage caused by shear forces or vibrations. Branch et al. (2016b) reported the impact of process failures and membrane integrity on virus removal efficiency, with the following findings:
To ensure more consistent pathogen removal by the membrane, regular selectivity tests and non-continuous direct monitoring of membrane integrity via pressure decay testing is recommended, in addition to continuous indirect online monitoring of membrane integrity (e.g., permeate water quality, turbidity, TOC) (Sharvelle et al., 2017). For selectivity tests, glass beads of a particular diameter are added to the membrane to determine the percent that pass through. Pressure decay testing is one of the most common tests used in the field to test for defects in the membrane, and can be performed in situ by applying air pressure to the membrane.
Other Operational Factors. Operational factors such as the solids retention time and the hydraulic retention time are assumed to have the same effect on pathogen reduction in MBR systems as they do for pathogen reduction during the biological part of similar activated sludge systems (Sidhu et al., 2015) (see Activated Sludge Chapter).
Overall mean and standard deviation of the log10 reduction values in MBR systems for different pathogen and indicator organisms are summarized in Table 3. Most of the data reported in the literature on pathogen reduction in MBR systems is for enteric viruses, bacteriophages, and fecal indicator bacteria. A few studies also reported log10 reductions of C. perfringens spores, a proposed indicator for protozoan pathogens (Branch et al., 2016b; Ottoson et al., 2006; Marti et al., 2011), and only one study reported the removal of actual protozoan pathogens (Ottoson et al., 2006). Likewise, only one study was found to report log10 reduction values for opportunistic and other bacterial pathogens, including Legionella and Arcobacter (Harb and Hong, 2017).
Table 3 reports the overall mean (average) log10 reduction values and standard deviations. However, the median values were very similar, indicating that the data did not have much skew. Also, the values reported in Table 3 are likely underestimates of the true reduction values for two reasons. First, in some of the studies cited in Table 3, the pathogen concentrations were reduced to below the detection limit, but not enough information was provided to treat the dataset using censored statistical models. Second, some authors reported log10 reductions over the entire system (including reduction due to predation in the aeration tank and by the membrane) while other authors reported log10 reductions by the membrane only. Given that the removal by the membrane has been shown to be 4 to 7 log10 units greater than the removal in the mixed liquor (Branch et al., 2016b), the distinction between overall reduction and reduction by the membrane only is minimal.
Fecal indicator bacteria removal is consistently high in these systems. For example, the Seine Morée MBR system in France consistently records 7 log10 reductions of E. coli. The review of the scientific literature revealed average E. coli and enterococci removal values of 6.1 log10 units in MBR systems. However, the systems are less efficient at reducing the concentration of viruses. The average log10 reduction of enteric viruses and bacteriophages in MBRs was found to be 3.3 and 3.4, respectively. Sano et al., (2016) conducted a meta-analysis of virus reduction in MBR systems, and reported that the reduction of norovirus GII was 3.35 log10 units (95% confidence interval: 2.39, 4.30), and that the reduction of enteroviruses was 2.71 log10 units (95% confidence interval: 1.52, 3.89). These values are similar to those shown in Table 3. Metagenomics analysis of DNA phages before and after an MBR indicated that no single group of DNA viruses is removed better than others (O’Brien et al., 2017). The summary statistics shown in Table 3 are compiled from values reported in the literature for systems with membranes that have a range of different pore sizes. Ultrafiltration membranes (pore sizes of 0.04 mm) have been shown to provide significantly different levels of virus reduction than microfiltration membranes (pore sizes of 0.45 mm) (Yin et al., 2015).
Membrane bioreactors produce secondary sludge at a rate that depends on the type of influent and the organic load applied. At SIAAP’s Seine Morée treatment plant in Paris, which receives domestic wastewater, 0.6 to 0.8 kg of sludge (as TSS) are produced for every kg BOD5 removed, and the concentration of sludge in the membrane tank generally varies between 6,000 and 12,000 mg/L VSS. Sludge must be removed daily from MBR systems to maintain proper operating conditions. Prior to disposal or reuse, the sludge must be treated (see chapter on Sludge Management). The concentration of pathogens in secondary sludge from MBR systems has not been well-studied. Nevertheless, more pathogens are caught on the membrane or in the cake layer of an MBR system compared to conventional activated sludge, where some of the pathogens (especially viruses) will be released in the clarified effluent. As such, secondary sludge from MBR systems will likely have with greater concentrations of pathogens compared to conventional activated sludge systems (Holbrook et al., 2005). Available data for viruses in sludge from MBR systems are shown in Table 4. Because of the high concentrations of pathogens in MBR secondary sludge, this sludge must be treated for additional pathogen reduction prior to being reused or returned to the environment (see Chapter on Sludge Management).
Among the different types of secondary wastewater treatment technologies, MBR systems provide very efficient pathogen reductions if they are maintained appropriately. Virus removal is the least efficient of all pathogen types. However, MBR systems can be designed and operated in a way that enhances virus removal efficiency as much as possible by using ultrafiltration membranes, monitoring the development of fouling, and conducting periodic selectivity and integrity testing. Fecal indicator bacteria should not be used as a surrogate for enteric virus removal in MBR systems, but bacteriophages appear to be an appropriate indicator for enteric virus removal in these systems. There are not enough data on the reduction of protozoan pathogens in MBR systems, but the reduction of C. perfringens spores is greater than that of viruses and bacteriophages but less than that of fecal indicator bacteria.
The efficiency of pathogen reduction in MBR systems will undoubtedly be influenced by local conditions, including the quality and composition of incoming untreated wastewater, operation and maintenance activities, troubleshooting capabilities, as well as socioeconomic and geographical factors that affect a community’s ability to provide proper maintenance. MBR is a complex treatment process that should be intensively validated before assigning log10 reduction credits. Any log10 reduction values reported herein should require local validation prior to being used for regulatory purposes.