Measurements of Hydrolysis in Moving Bed Biofilm Reactor Carriers - Evaluation by means of Oxygen Uptake Rate Measurements

Transcription

1 Water and Environmental Engineering Department of Chemical Engineering Measurements of Hydrolysis in Moving Bed Biofilm Reactor Carriers - Evaluation by means of Oxygen Uptake Rate Measurements Master s Thesis by Kristina Henriksson and Oscar Tenfält February 2011

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3 Vattenförsörjnings- och Avloppsteknik Institutionen för Kemiteknik Lunds Universitet Water and Environmental Engineering Department of Chemical Engineering Lund University, Sweden Measurements of Hydrolysis in Moving Bed Biofilm Reactor Carriers - Evaluation by means of Oxygen Uptake Rate Measurements Master Thesis number: by Kristina Henriksson and Oscar Tenfält Water and Environmental Engineering Department of Chemical Engineering February 2011 Supervisors: Professor Jes la Cour Jansen Ph.D. Eva Tykesson Examiner: Associate professor Karin Jönsson Postal address: Visiting address: Telephone: P.O Box 124 Getingevägen SE Lund Sweden, Telefax: Web address:

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5 Summary Today the need for clean water is rapidly increasing as the world s population grows by each year. The new awareness about the decreased rainfall that is expected in large parts of the world due to climate change and urbanization, which accumulate large amounts of people in cities, calls for efficient wastewater treatment facilities. To remove organic matter in wastewater activated sludge is the dominating biological treatment method, in which the microorganisms consume organic substances suspended in the solution. After the water is treated the microorganisms are settled and recycled in the process. Another method that is becoming more common is the Moving Bed Biofilm Reactor, in which the biofilm grows inside carriers of polyethylene, which in addition to protecting the biofilm from friction forces, allow for a larger biomass in the treatment process. In this master thesis the aim was to determine the extent to which particulate organic matter in wastewater is hydrolyzed in an MBBR carrier process by means of bacterial respiration rates. A new method based on Oxygen Uptake Rate (OUR) measurements was developed and important aspects concerning the method were identified. The method was then used for measurements of hydrolysis during different operating conditions. By comparing the bacterial respiration rates in wastewater containing particulate organic matter and filtrated wastewater, the hydrolysis was qualitatively determined. An important parameter is the oxygen level, which must be as high as possible and similar in all reactors that are to be compared. Also, the biofilm used must be equal and preserved throughout the experiment. The method was found to measure hydrolysis accurately. The method was finally tested in two experiments, which investigated the influence of added particles and dissolved carbon on hydrolysis. The results suggest that the hydrolysis is independent both of organic loading and the availability of easily accessible carbon. i

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7 Preface This report is the result of a master thesis in Environmental Engineering performed at Water and Environmental Engineering, Department of Chemical Engineering, Lund University. Hydrolysis of particulate organic matter in Moving Bed Biofilm Reactor carriers was determined by Oxygen Uptake Rate measurements. The master thesis was based on a literature review and laboratory experiments performed at AnoxKaldnes AB in Lund. The work was supervised by Ph. D. Eva Tykesson at AnoxKaldnes AB and by Professor Jes la Cour Jansen at Water and Environmental Engineering. Several people have contributed to this master thesis and we would like to thank you all for your support. We want to give special thanks to Eva Tykesson for initiating the project, for introducing us to the pilot plant in Kävlinge, from which wastewater samples and biofilm carriers were collected, and for her valuable comments and thoughts on our work. Without the initiative of Eva Tykesson, this project would not have been realized. Further, we want to thank Jes la Cour Jansen for guiding us through challenging discussions, for supporting us whenever needed with comments and thoughts on our work. Jes knowledge and dedication has helped us on numerous occasions. Thanks to the staff at AnoxKaldnes AB for being so cheerful and helpful, and for showing so much interest in our work. It has been a pleasure getting to know you all while we have been working with our master thesis. We would like to thank Jenny for guiding us through the COD as well as the TSS and VSS measurement procedures and for supplying us with several wastewater samples and carriers from the pilot plant in Kävlinge. We would also like to thank Carina and Maj-Elén for the introduction to the laboratory at AnoxKaldnes and for the information on current safety regulations. Thanks also to Magnus for interesting comments on our work and to Stig for supplying us with the timer we used to start and stop the aeration in our experiments. A big thank you to Petter, the photographer who took the picture on the front page. Finally, a huge thank you to our families and friends who have supported us through this challenging task. Lund Kristina Henriksson and Oscar Tenfält iii

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9 Table of contents 1 INTRODUCTION Aim Limitations BACKGROUND Particles in wastewater Moving Bed Biofilm Reactor Biofilm kinetics The fate of particles Hydrolysis Enzymatic hydrolysis Location of hydrolysis Rate of hydrolysis Oxygen Uptake Rate MATERIALS AND METHODS Sampling Storage of samples Experimental procedure Experimental setup Execution of the experiments Processing of data Measurements of COD Measurements of total suspended solids and volatile suspended solid Measurements of volatile fatty acids (VFA) Calculations Oxygen consumption Oxygen dependence METHOD DEVELOPMENT Experiment 1 - Introduction to the Oxygen Uptake Rate method Purpose Expected results Changes to setup Procedure v

10 4.1.5 Results from the introductory experiment Summary of experiment Experiment 2 - Importance of the oxygen level Purpose Expected results Changes to setup Procedure Results and from the second experiment Summary of experiment Experiment 3 - Oxygen dependence Purpose Expected results Changes to setup Procedure Results from oxygen dependence experiment Summary of experiment Experiment 4 - Repeatability test Purpose Expected results Changes to setup Procedure Results from the repeatability experiment Summary of experiment Experiment 5 - Hydrolysis experiment Purpose Expected results Changes to setup Procedure Results from the repeatability experiment Summary of experiment Evaluation of the method HYDROLYSIS EXPERIMENTS Experiment 6 - Significance of particles Purpose Expected results Changes to setup Procedure Results from the investigation of particles significance Summary of experiment Experiment 7 - Influence of dissolved carbon Purpose Changes to setup vi

11 5.2.3 Procedure Results from the investigation of dissolved carbons influence Summary of experiment DISCUSSION CONCLUSIONS SUGGESTIONS FOR FURTHER RESEARCH REFERENCES APPENDIX A - REACTOR CONTENTS... I APPENDIX B - COD MEASUREMENTS... III APPENDIX C - OXYGEN CONSUMPTION... V APPENDIX D - TEST OF OXYGEN METERS... VII APPENDIX E - TSS/VSS AND VFA MEASUREMENTS... IX APPENDIX F - HYDROLYSIS OF PARTICLES... XI APPENDIX G - ARTICLE... XIII vii

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13 1 Introduction Clean water, which is essential for both human and animal life, is today a limited resource in large areas of the world. By 2008 the world population reached 6.7 billion people according to WHO s World Health Statistics (2010), and by 2011 we are, by UN s medium estimate, expected to become 7 billion people on earth (United Nations, Dep. of Economic and Social Affairs, 2010). The world s growing population places new demands on the supply of clean water as well as on treatment measures. Today most people reside in urban areas and the requirements for wastewater treatment are rapidly increasing. In wastewater treatment plants, combinations of physical, biological and chemical methods are used to purify the water. The biological treatment step reduces nitrogen, phosphorous, bioavailable carbon and other organic contaminants with the aid of microorganisms (Gillberg et al., 2003). The most common and well-known biological wastewater treatment process is the activated sludge process (Jonstrup et al., 2010). Basically, the activated sludge process is based on an aerated tank, in which organic matter is degraded by suspended microorganisms (Jonstrup et al., 2010). The sludge is then separated in a clarifier and excessive sludge is removed from the process (Jonstrup et al., 2010). In order to retain the bacterial fauna in the process, some of the separated sludge is recycled to the aerated tank (Jonstrup et al., 2010). Although still less common than activated sludge processes, the Moving Bed Biofilm Reactor (MBBR) is becoming increasingly popular. By 2000, some 100 wastewater treatment processes around the world utilized the MBBR concept (Ødegaard et al., 2000). To date, more than 500 MBBR processes based on the use of carrier elements are found in more than 50 countries (AnoxKaldnes, 2009). In difference from in activated sludge systems, the biomass in MBBR processes is retained. In order to determine the extent to which particulate organic matter in wastewater is hydrolyzed in an MBBR carrier process, a new method based on Oxygen Uptake Rate (OUR) measurements is developed. There are four experimental approaches in research concerning the quantification of hydrolysis, look at enzymes, hydrolytic fragments, bulk parameters or bacterial respiration rates (Morgenroth et al., 2002). Using one of the first two approaches, the mechanisms of the process can be determined often using artificial substrates that facilitate to isolate a specific mechanism (Morgenroth et al., 2002). The result is therefore often not usable in real conditions where the substrate has a mixed composition. The second two can give information on the whole process but not give information on specific parts of the process (Morgenroth et al., 2002). In this thesis a method to measure hydrolysis using the bacterial respiration rates will be developed. According to Morgenroth et al. (2002) it is useful to do the research using a mixed substrate, a mixed bacterial culture and to compare biofilm based processes with the traditional activated sludge. 1.1 Aim The main focus of this master thesis was the development of a new method for determination of the extent to which particulate organic matter in wastewater is 1

14 hydrolyzed in an MBBR carrier process. The applicability of the method to measure hydrolysis in the MBBR process was then to be evaluated. After testing the applicability of the method, it was to be applied to different operating conditions. The importance of three different concentrations of particles with regard to hydrolysis as well as whether hydrolysis is inhibited at elevated levels of dissolved organic matter was then to be investigated. 1.2 Limitations Hydrolysis occurs under versatile circumstances but this master thesis focuses on enzymatic hydrolysis in aerobic wastewater treatment processes based on an MBBR process using carriers. 2

15 2 Background 2.1 Particles in wastewater Wastewater is typically discharged from a number of diverse sources and as a result it contains a variety of pollutants, including organic matter. Generally, the organic material constitutes about 40-60% proteins, 25-50% carbohydrates and 10% lipids (Haldane & Logan, 1994). Depending on their size, these compounds can be divided into four fractions - soluble (<0.08 µm), colloidal particles ( µm), supercolloidal particles (1-100 µm) and sedimenting particles (>100 µm) (Gillberg et al., 2003). In the following sections, organic matter will simply be regarded as the sum of two fractions - particulate organic matter (particles) and dissolved organic matter. Any organic material with a size greater than 0.8 µm is referred to as particulate. Particles larger than 100 µm are to a large extent removed in the primary sedimentation, which often is placed before the biological treatment in wastewater treatment plants (Morgenroth et al., 2002). Therefore particles mainly in the size range 0.8 to 100 µm are discussed in this chapter. Whether organic matter is available to microorganisms is dependent on the size and composition of the material. It is common to distinguish between slowly biodegradable organic matter and easily biodegradable organic matter, of which the latter often has a mass less than 1000 amu 1 (Morgenroth et al., 2002). The slowly biodegradable, on the other hand, can be presumed to be in the range 1000 amu to 100 µm (Morgenroth et al., 2002). This way of classifying organic matter indicates whether microorganisms in the wastewater may utilize it directly by uptake through the cell membrane, as 1000 amu is the upper limit for direct uptake (Confer & Logan, 1998; Morgenroth et al., 2002). Another way of defining the upper limit for direct uptake is by particle size. According to Janning et al. (1997), particles smaller than µm can cross the cell membrane of microorganisms. 2.2 Moving Bed Biofilm Reactor The AnoxKaldnes MBBR is used in wastewater treatment processes such as nitrification, denitrification and BOD-removal (AnoxKaldnes, 2009). The technology is based on the use of carrier elements made of a polyethylene that has a density slightly lower than that of water (AnoxKaldnes, 2009). Thereby the carriers are easily kept in suspension by aeration in aerobic processes or by mixing with stirrers in anoxic or anaerobic processes (AnoxKaldnes, 2009). Although most biological wastewater treatment processes are based on activated sludge, the MBBR concept is becoming increasingly popular and to date it has been applied to more than 500 wastewater treatment processes around the world 1 Atomic mass unit 3

16 (AnoxKaldnes, 2009). The biofilm is constituted by extracellular polymeric substances (EPS) holding together a diverse culture of microorganisms, whose composition reflect the chemical composition of the wastewater (Janning, 1998). The application of the biofilm principle normally yields a higher biomass to volume ratio than systems based on activated sludge (la Cour Jansen, 2011). Thus, in order to achieve a certain treatment, an MBBR process requires less volume than corresponding activated sludge process. Furthermore, the design of the carriers limits the impact from physical stress on the biofilm which thereby allows for higher flows through the process. There is always some loss of biomass with the effluent, in particular from the exposed surface layer of the biofilm. Most of the biofilm is however retained in the MBBR as a result of the carrier design (AnoxKaldnes, 2009). The main drawback with biofilm processes in general is that only a small fraction of the biofilm is active. In MBBR, however, the use of carriers compensate for part of this effect by allowing more biomass and thereby more surface area per unit volume Biofilm kinetics The substrate removal kinetics in biofilm applications is strongly dependent on the concentration of substrate in the wastewater being treated. This is illustrated in Figure 2.1, which shows the development of the kinetic description from a 1 order expression at low concentrations to a 0 order expression at very high concentrations. The transition from low to very high substrate concentration is described with a ½ order expression. Figure 2.1: The kinetic description with reaction rate as a function of the substrate concentration (Henze et al, 1997). As seen in the figure, the substrate removal rate is limited by the substrate concentration only at low concentrations where a small change in concentration gives a proportional change in the degradation (Ødegaard et al., 2000). At high substrate concentrations the rate is limited by the diffusion of substrate into the biofilm. Thus, as the concentration increases the kinetics begins to shift from being concentration dependent to being diffusion dependent and eventually the kinetics becomes independent of the substrate concentration, this is described by ½ order kinetics 4

17 (Ødegaard et al., 2000). At very high substrate concentrations the enzymatic efficiency restrains the removal rate - 0 order dependence (Ødegaard et al., 2000). Although the kinetics in biofilm processes is normally described as above, it should be pointed out that the composition of the substrate in the wastewater will determine its kinetic characteristics (Ødegaard et al., 2000). Diffusion is believed to be the most important mass transfer phenomenon and is thus normally considered in kinetic descriptions (Larsen, 1992). Other transport mechanisms such as advective transport, on the other hand, are usually not regarded (Larsen, 1992). 2.3 The fate of particles The majority of carbon input to wastewater treatment plants constitutes particulate organic matter in the form of slowly biodegradable organic matter (Insel et al., 2003). Particles entering a MBBR are either degraded by micro-organisms in the biofilm or pass straight through the process. The particles may be completely degraded and taken up by microorganisms but they could also be partially degraded and then released back into the bulk liquid. The size of the organic fragments resulting from the degradation determines whether the microorganisms in the process may utilize the degradation products directly. A fraction of the partially degraded particles will join the undegraded particles that pass straight through the process, most of the partially degraded particles are however likely to come in contact with the biofilm again for further degradation. Completely degraded substrate is transported through the bacterial membrane, where it is used for respiration and production of new biomass. Almost 50% of the energy in the substrate is bound in new biomass (Jonstrup et al., 2010). Biomass eventually detaches from the carrier surface mainly due to shear forces and degradation in the interior of the biofilm (la Cour Jansen, 2011). Thus, to some extent, biodegradation transforms organic matter in influent water to particles of biomass. 2.4 Hydrolysis The process in which an organic molecule is split into smaller parts by addition of water is called hydrolysis (Morgenroth et al., 2002). The water molecule is divided into a hydrogen and hydroxyl ion and the hydroxyl ion performs a nucleophilic attack on a bond, splitting the molecule in two parts (Ellervik & Sterner, 2007). The hydrogen and hydroxyl ion then binds to each part of the divided molecule (Ellervik & Sterner, 2007). In the context of wastewater treatment, hydrolysis includes all processes contributing to degradation of organic matter (Morgenroth et al., 2002). 2.5 Enzymatic hydrolysis In a MBBR process, degradation of particulate organic matter is aided by extracellular enzymes produced by the microorganisms present in the process. Complete degradation of individual particles as well as partial degradation of several particles is catalyzed by extracellular enzymes. Further, out of 197 identified extracellular enzymes, 145 have 5

18 been found to be hydrolytic (Schomburg et al., 1997 cited in Morgenroth et al., 2002, p.28). The hydrolytic enzymes are either attached to the bacterial membrane or suspended in the bulk liquid (Confer & Logan, 1998). Complete degradation of more complex particulate organic matter such as polysaccharides may require a mixture of hydrolytic enzymes (Haldane & Logan, 1994). The large number of hydrolytic enzymes is therefore essential for the microorganisms in wastewater to be able to utilize a wide range of organic compounds. Bacterial production of enzymes is normally stimulated by environmental factors such as substrate availability, but in some cases the production of enzymes carry on regardless of external effects (Larsen, 1992). Further, Goel et al. (1999) found that the synthesis of enzymes is influenced by the oxygen level, while already synthesized enzymes are unaffected by the availability of oxygen. The hydrolysis rate is however independent of the oxygen level according to the results presented by Goel et al. (1999) Location of hydrolysis Organic particulate matter that is too large to diffuse into the biofilm is degraded either at the biofilm surface by enzymes that are membrane attached or in the bulk liquid by extracellular enzymes excreted by the bacteria. Rohold & Harremoës (1993) investigated the importance of residence time by means of OUR and found that a decrease in retention time leads to a decrease in OUR. The interpretation was that there was a wash out of extracellular enzymes from the bulk during the experiments, reducing the hydrolytic activity and thus the OUR (Rohold & Harremoës, 1993). Based on this interpretation, Rohold & Harremoës (1993) concluded that hydrolysis of particulate organic matter takes place in the bulk liquid. However, since OUR only measures complete hydrolysis followed by microbial respiration, a wash out of hydrolytic fragments would have the same effect as a wash out of enzymes. Thus, a decrease in OUR is not proof of a lower hydrolysis rate, it could as well be explained as loss of hydrolytic fragments from the system, leading to a lowered respiration. Confer & Logan (1998) measured merely 3-7 % of the total hydrolytic activity in the bulk, leading to the conclusion that hydrolysis takes place almost exclusively at the biofilm surface. Further, Confer & Logan (1998) found the hydrolysis rate to be much higher at the biofilm surface than at the surface of sloughed biofilm or in cell-free environments. Several other studies performed in natural waters during support these findings (Confer & Logan, 1998). The extracellular enzymes released to the bulk liquid are always at risk of being prematurely washed out of the reactor due to the hydraulic retention time, while those attached to the membrane are retained during the entire lifetime of the cells. Thereby, from an energy efficiency point of view, it is better for bacteria to hold on to enzymes than to release them into the bulk. Also, enzymes released to the bulk liquid can be utilized as carbon source by bacteria (Confer & Logan, 1998). According to Boltz & La Motta (2007), organic particulates attach to the biofilm surface due to bioflocculation. Further, Boltz & La Motta (2007) regard bioflocculation in biofilm reactors and particle bioflocculation in activated sludge reactors as similar 6

19 processes and thereby validate the hypothesis that the EPS in the biofilm bind particles with results from studies on activated sludge performed by La Motta et al. (2003, 2004). Bioflocculation is a process in which chemical bonding arises between the EPS and the organic particulates (Boltz & La Motta, 2007). The particles are then hydrolyzed by extracellular enzymes and the hydrolytic fragments are, depending on their size, either taken up by the microorganisms in the biofilm or released to the bulk solution (Confer & Logan, 1998). This is consistent with the results from several other experiments, which demonstrated that hydrolysis of proteins and polysaccharides occurs in contact with biofilm or sludge flocs in activated sludge (Confer & Logan, 1998). However, with increasing molecular weight the diffusion into the EPS becomes limiting, which results in a relocation of the hydrolytic activity from the membrane surface to the EPS constituting the biofilm surface (Dimock & Morgenroth, 2006). Dimock & Morgenroth (2006) suggests that the microorganisms presumably release enzymes into the EPS. By excreting extracellular enzymes into the EPS, the microorganisms would increase the rate at which high molecular compounds are hydrolyzed and consumed. Also, the EPS is flexible and can enfold larger particles, which are thereby accessible to hydrolysis by the enzymes in the EPS (Dimock & Morgenroth, 2006) Rate of hydrolysis Hydrolysis is limiting for substrate degradation as the rate at which it proceeds is lower than the rate of uptake of fully degraded substrate by microorganisms (Okutman et al., 2001). Morgenroth, et al. (2002) highlights the importance of particle size for bioavailability, mass transfer and attachment of particles. Further, Dimock & Morgenroth (2006) performed experiments, which demonstrated that particle size plays an important role in the rate of hydrolysis in activated sludge processes. During degradation of particulate organic matter smaller particles are formed and released back into solution, increasing the surface to volume ratio of the substrate available for hydrolysis, making it more accessible to microorganisms (Dimock & Morgenroth, 2006). Smaller particles are thereby hydrolyzed more rapidly than larger particles. Size seems to have smaller influence on the rate of hydrolysis degrading macromolecules, as the size primarily affects the diffusion to the biofilm surface. Larger molecules have a small diffusion coefficient making the overall degradation rate slower (Kommedal et al., 2006). The physical properties, such as diffusion, gain more importance in the degradation rate as the hydrolytic fragments disperse into the bulk liquid (Haldane & Logan, 1994). Dimock, & Morgenroth (2006) showed an increase of hydrolysis rate with time, which could perhaps be explained by the increase in hydrolytic fragments in the bulk liquid as the process proceeds. Priest, (1984) as cited by Janning et al. (1997), found that the hydrolysis rate could be diminished due to enzyme inhibition, as a response to addition of readily available carbon. 2.6 Oxygen Uptake Rate Of the organic substances consumed in a wastewater treatment process one part is used for biomass production while the other is used for respiration. The oxygen used for 7

20 respiration can be determined by measuring the decrease in oxygen level in the process when no air is supplied. By calculating the slope of the oxygen concentration curve during several unarerated intervals, the Oxygen Uptake Rate (OUR) and oxygen consumption connected to respiration is found. OUR can be used to determine for instance the performance of a treatment plant and wastewater characteristics and combined with additional analytical methods more information can be retained about the processes (Hagman & la Cour Jansen, 2007). An important estimation made is that the substrate able to penetrate the bacterial membrane is immediately utilized for respiration or biomass production and that no accumulation or storage of PHA or glycogen occurs (Dimock & Morgenroth, 2006). Dimock & Morgenroth (2006) performed experiments with acetate, BSA 2 and egg whites and only observed internal storage of PHA when using acetate. It is therefore unclear whether the influence of storage is of significance in this master thesis since wastewater is composed of diverse material. Whether a specific substance is stored and if it constitutes a significant part of the organic material in the wastewater is hard to determine. 2 Bovine serum albumin 8

21 3 Materials and methods This chapter includes the procedures that were undertaken in the experimental part of the master thesis. However, since the main goal was to find a method that can be used to measure hydrolysis of particles in wastewater, several different experiments were performed. All basic information on the experimental work is covered by the following sections while details specific on individual experiments are found in the next chapter, 4 Method development. 3.1 Sampling Kaldnes carriers of model K3 and wastewater were sampled from AnoxKaldnes pilot plant at the wastewater treatment plant in Kävlinge on the day of the experiment. The carriers were collected in plastic containers and in order to preserve the carriers, the containers were filled with effluent water. Plastic bottles with a volume of 1 l were used for all wastewater samples. Further, the inflow of wastewater to the pilot tank was measured manually with a plastic pitcher holding 3 l of water and a stop watch. All flow measurements are found in Appendix E. Figure 3.1: The hydrolysis tank at the wastewater treatment plant in Kävlinge is the sampling location Storage of samples Particulate COD in wastewater samples is hydrolyzed and consumed by microorganisms in the wastewater as long as oxygen is available. Therefore, fresh wastewater rather than wastewater that has been stored is preferred for experimental purposes. Whenever samples had to be stored before use, they were put in a refrigerator keeping a temperature of 4 C. The microbial activity in the samples was thereby slowed down, reducing the loss of substrate in the samples. Filtered samples have less biomass present in the bulk water and were thereby not as affected by consumption during storage. 9

22 3.2 Experimental procedure Experimental setup The experiments were based on an arrangement with two reactors run in parallel, see Figure 3.2. Mantled glass beakers with an inner diameter of 9 cm functioned as the reactors in which 1 l of wastewater was aerated by aquarium pumps and stirred by magnetic mixers using fleas with a length of 7 cm. Diffuser stones were connected to the tubings through which air was supplied in order to achieve gentle aeration with fine air bubbles in the reactors. Figure 3.2: Experimental setup: 1. magnetic stirrer, 2. 1 l glass beaker, 3. Probe, 4. HQ40d meter, 5. aquarium pump, 6. Flow meter. Even though no diffusers are used in the pilot plant, sufficient amounts of air diffuse into the water since the air bubbles have to travel several meters to reach the surface. In the laboratory scale reactors, on the other hand, the water column was just 20 cm. Thus, to achieve even distribution of oxygen in the reactors, the residence time as well as the contact area to volume ratio was increased by using fine air bubbles. The airflow and subsequently the aeration intensity in the reactors were controlled with rotameters from Dwyer and the airflow was measured with flow meters from TSI Instruments Ltd. Further, the water and carrier elements were stirred by agitators during the experiments, see Figure 3.2. When the aeration was turned on, it also contributed to the agitation. The consumption of oxygen during the experiments was studied using OUR methodology, see 2.6 Oxygen Uptake Rate. HQ40d Digital Multi-Parameter Meters from Hach were used to measure the oxygen concentration in the reactors during the experiments. 10

23 3.2.2 Execution of the experiments 50 carriers were added to each reactor and then, in order to determine the endogenous respiration in the reactors, the first part of the experiments, the pre-period, was run with water that had no external carbon source. External carbon was then added and the consumption of oxygen resulting from increased microbial respiration was studied. When the level of respiration returned to that of endogenous respiration, the external carbon had been consumed and the experiments were terminated. The consumption of particles takes several days, thus the particles were not fully degraded during the experiments, but when the degradation is so slow that the oxygen consumption is not detectably higher than the endogenous respiration, the experiment is over. All experiments were carried out at room temperature. Filtering 1.6 µm glass fiber filters were used to filter wastewater samples. Thus, according to the definition of particulate and dissolved COD presented in 2.1 Particles in wastewater, hydrolysis of colloidal particles and soluble organic matter too large for direct uptake by microorganisms was excluded in the experimental part of the master thesis. However, for practical reasons, COD with a size greater than 1.6 µm will be referred to as particulate while COD with a size less than 1.6 µm will be referred to as dissolved in 4 Method development and 5 Hydrolysis experiments. Oxygen concentration measurements Oxygen concentration measurements were taken with ten second intervals in all experiments except the first one, in which measurements were taken every thirty seconds. Further, the HQ40d meters have a maximum storage capacity of 500 data points, thus data had to be transferred to a USB memory during the experiments. By timing the data transfers with aerated intervals, loss of important data was avoided. The data transfers are seen as gaps in the graphs illustrating how the oxygen concentration varies with time during the experiments presented in 4 Method development and 5 Hydrolysis experiments. A drawback with the oxygen meters is that bubbles might get trapped in the probe measuring the oxygen level, influencing the measurements Processing of data The data logs from the oxygen concentration measurements were inserted into Excel and the maximum OUR was calculated for each unaerated interval in the experiments. Due to differences between the experiments concerning the characteristics of the data, it was difficult to apply a general rule concerning the choice of data for the calculations. Five to ten data points were chosen from each unaerated interval and, to the greatest extent possible, the OUR was calculated at high oxygen levels. The OUR was then plotted against time and, based on the level of endogenous respiration, the amount of oxygen consumed during respiration of the carbon source was determined. The oxygen dependence was also calculated according to the method described in Oxygen Dependence. The addition of an external carbon source, and thus from which point and 11

24 on the oxygen consumption was calculation, is marked as a vertical black line in the OUR graphs Measurements of COD COD was measured in the inlet and outlet water from the pilot plant as well as in the reactors during the experiments. Generally, both unfiltered and filtered water samples were taken from the pilot plant, while filtered water samples exclusively were taken from the reactors right after addition of external carbon and at termination of the experiments. Dr. Lange cuvette test LCK 114 was then used for analysis of the COD content in the water samples. The results from all COD measurements are found in Appendix B Measurements of total suspended solids and volatile suspended solid The TSS and VSS content of the biomass in wastewater samples were determined by using a series of steps. Firstly, the wastewater was filtered through a 1.6 µm filter with known weight. Then, in order to evaporate the water in the filter, the filter was dried in an oven at 105 C for 24 hours. The filter was weighted once again and the TSS content was calculated as the difference in weight before usage and after drying divided by the volume of filtered wastewater. Thereafter the filter was put in an incinerator at 550 C for 24 hours, only leaving ash and inorganic matter. The VSS content was then found as the difference in weight between the dried and incinerated filter divided by the volume of filtered wastewater. The procedure is described in the Swedish Standard SAP Measurements of volatile fatty acids (VFA) In experiment 4 and 5, the VFA was measured once every half hour from the moment carbon was added until the experiment finished. The results are found in Appendix E. 3.3 Calculations Oxygen consumption When determining the oxygen consumption, each calculated OUR was assumed to be constant for a certain period of time. The first time interval ranged from the moment external carbon was added in the experiments to the point in time located in between the two following OUR. The remaining time intervals then ranged according to the same pattern, which was from in between the first and second OUR after addition of carbon to in between the third and fourth and so on. After the time intervals had been established, the increase in OUR from the reference level (endogenous respiration) due to addition of external carbon was calculated: Whenever the OUR was equal to or lower than the reference level, OURref, OUR was set to zero. The oxygen consumption was then calculated as the sum of the first OUR 12

25 multiplied with the first time interval, the second OUR multiplied with the second time interval and so on; n is the number of OUR data points after the addition of external carbon in the experiments Oxygen dependence The oxygen dependence of OUR was qualitatively determined based on the results from experiment 3, 4 and 5. OUR as well as average oxygen concentrations were calculated based on sets of five oxygen concentration measurements. Linear regression was then used to determine whether there is a significant relationship between OUR and the oxygen concentration. Further, trends in the oxygen dependence as well as shifts between oxygen limitation and carbon limitation were studied. All graphs and tables are found in the next chapter, Method Development. Numbers with poor correlation coefficients are regarded as irrelevant and subsequently they are in brackets. 13

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27 4 Method development The purpose of the method development was to find a way to measure hydrolysis in wastewater from AnoxKaldnes pilot plant. The main idea is that the Oxygen Uptake Rate, OUR, is lower in a filtrated wastewater sample than in an unfiltered sample of the same volume, due to the absence of particles in the filtrated sample. Thereby it should be possible to measure the contribution to the OUR by the particles by comparing the filtrated and unfiltrated wastewater. This chapter includes five experiments designed to measure the hydrolysis as closely as possible. At the end of the chapter, parameters that were identified as especially important are discussed. 4.1 Experiment 1 - Introduction to the Oxygen Uptake Rate method Purpose The initial experiment was a trial and error experiment aiming at introducing the OUR method, but more importantly it was performed to identify relevant factors influencing the results Expected results Prior to the experiment, the importance of factors such as filtration, aeration intensity, stirring intensity and storage time in the cool room was unknown. Therefore, the results from this experiment were expected to only give an indication of the possibility to measure hydrolysis of particulate organic matter in an MBBR process Changes to setup The setup was as described in 3 Materials and methods, with the exception that no flow meters were used to measure the air flow from the pumps. Further, the two reactors were run with the following carbon sources: Reactor 1A l of filtered outlet water and 0.25 l of filtered inlet wastewater Reactor 1B l of filtered outlet water and 0.25 l of unfiltered inlet wastewater Procedure 1 l of inlet wastewater, 1 l of outlet wastewater and 100 carriers was collected at Kävlinge. The container with influent wastewater was placed in the cool room in order to slow down the microbial activity in the water. When the carriers were added to the reactors, no effort was put into adding an even mix of carriers from the top, middle and bottom layer in the plastic container, in which they were brought. The first 50 were put in one reactor and then the other 50 were put in the other reactor. 0.5 l of the effluent wastewater was then filtered and split between two reactors l in each. Finally, to each of the reactors, 0.5 l of tap water was added and the aeration and stirring started. The aeration was kept on for 14 minutes and then it was turned off for 6 minutes manually throughout the entire experiment. After the pre-period started, 0.25 l of the inlet water was filtered for use in reactor 1A. The inlet water was then placed in the cool room again for the remaining time of the one 15

28 hour long pre-period. Once the pre-period ended, the filtered water was added to reactor 1A while 0.25 l of unfiltered water was added to reactor 1B Results from the introductory experiment Figure 4.1 shows how the oxygen concentration in the reactors changed throughout the experiment. The oxygen concentration reached a higher level in 1A than in 1B already during the pre-period, which was probably the result of higher aeration intensity in 1A than in 1B during the experiment. What caused the difference is unclear, but one possible explanation is that the pump used to aerate 1A had a higher capacity than the one used in 1B. Another one is that the diffuser stone used in 1B had less porosity than the one used in 1A. After addition of carbon, the oxygen concentration decreased rapidly in both reactors due to increased microbial activity. Figure 4.1: Oxygen concentration as a function of time. OUR The oxygen was consumed at a higher rate in 1B than in 1A during the first unaerated interval after the carbon was added. This observation is confirmed by Figure 4.2, in which the OUR in the two reactors during the experiment is presented. At addition of carbon, the OUR in 1B reached a significantly higher level than in 1A. There was only a clear difference in OUR between the two reactors during a short period of time after the carbon was added though. 16

29 Figure 4.2: OUR as a function of time. Calculations of the oxygen consumption in the two reactors do, however, suggest that twice as much oxygen was consumed in 1B than in 1A during the experiment, see Appendix C - Oxygen consumption. This could indicate the microbial activity in 1B increased due to respiration of hydrolyzed particles when unfiltered wastewater was added to the reactor Summary of experiment 1 This experiment was successful in terms of acquiring knowledge how to utilize the OUR method when studying hydrolysis of particles in an MBBR process. The relevance of the results however, is arguable due to a number of uncertainties. These uncertainties were identified as important factors that need to be taken into consideration in order to attain results that can be compared. It was found important to have the same oxygen level in both reactors, but another experiment is needed to determine an appropriate level. 4.2 Experiment 2 - Importance of the oxygen level Purpose The aim with this experiment was to determine whether the OUR is dependent on the oxygen level in wastewater. Two different oxygen levels - 6 mg O2/l and 3 mg O2/l - were chosen for the study. Furthermore, the possibility of having shorter aerated and unaerated intervals than in the first experiment was evaluated by measuring the oxygen concentration every ten seconds instead of every thirty seconds that was the case in last experiment Expected results The oxygen concentration graphs based on the results from the initial experiment revealed a nonlinear decrease in oxygen concentration, see Figure 4.1. The slope of the curve decreases gradually during the descents representing the unaerated intervals of 17

30 the experiment, indicating oxygen limitation in the reactors at lower oxygen levels. Based on these observations, the OUR was expected to be lower in the reactor kept at 3 mg O2/l than in the reactor kept at 6 mg O2/l Changes to setup No changes were made to the basic setup of the experiment and the two reactors were run with the same carbon source, which was 0.5 l of unfiltered inlet water from the pilot plant. The reactor run at the higher oxygen level is referred to as 2A, while the one run at the lower oxygen level is referred to as 2B. Reactor 2A l unfiltered inlet wastewater 5< O2<6 mg /l. Reactor 2B l unfiltered inlet wastewater 2< O2<3 mg/l Procedure 1 l of influent wastewater and 100 carriers were sampled at Kävlinge and brought back to the laboratory. Before the experiment started, the carriers were aerated in glass bottles filled with tap water for ten minutes to achieve saturation of the biofilm. This was necessary since no pre-period was run prior to the addition of carbon source to the reactors in this experiment. Otherwise, changes in the oxygen level in the reactors would be the result of a combination of saturation of the biofilm and microbial activity, of which only the latter was of interest in this experiment. The wastewater as well as the saturated carriers was equally split between two reactors and like in last experiment no effort was put into achieving an even distribution of carriers from the top, middle and bottom layer in the plastic container, in which they were brought. 0.5 l of tap water was then added to each of the reactors and the aeration was turned on. Outlet water was assumed to be unnecessary in this experiment since the biofilm got access to the external carbon source already at the very beginning of the experiment. When the experiment started, the oxygen level was close to 5 mg O2/l in both reactors so it had to be adjusted to the desired levels of 6 and 3 mg O2/l. The intention was to reach the higher level in reactor 2A with aeration and to reach the lower level in reactor 2B with a mixture of air and nitrogen gas. According to the flow meters used in the experiment, the flow of air to 2A and 2B was 1.18 l/min and 0.95 l/min, respectively. Lowering the oxygen level in reactor 2B with nitrogen gas was however unsuccessful because the valve to the tube containing nitrogen gas that was connected to reactor 2B was not properly opened during the whole experiment, which prevented the nitrogen gas from reaching the reactor. Thus, the oxygen level was lowered to 3 mg O2/l by microbial consumption instead of by nitrogen gas. The oxygen concentration was then manually controlled during the one and a half hour long experiment so that the intervals 5 to 6 mg O2/l and 2 to 3 mg O2/l could be studied. Measurements of the oxygen concentration were taken every ten seconds. 18

31 4.2.5 Results and from the second experiment The oxygen concentration in the reactors as a function of time is found in Figure 4.3. On average close to equally long aerated and unaerated intervals were required to keep the oxygen concentration within the desired range in both reactors. Figure 4.3: Oxygen concentration as a function of time in 1A-B. OUR Figure 4.4 indicates the microbial activity in 2B was suppressed due to the lower oxygen concentration leading to a lower oxygen consumption in 2B, than in 2A, during the experiment. However, a small part of the difference in OUR between the reactors could be explained by uneven distribution of the inlet water and thus the COD used in the experiment. Figure 4.4: OUR as a function of time in 1A-B. From the results presented in Figure 4.4, the oxygen consumption in 2A was found to be about 4.5 mg O2 higher than that in 2B (Appendix C). 19

32 4.2.6 Summary of experiment 2 The hypothesis that OUR is dependent on the oxygen concentration in the wastewater was verified by this experiment. Most oxygen was consumed in reactor 2A, in which the oxygen concentration was kept within the range 5 to 6 mg O2/l. It is best to keep the oxygen level in the reactor as high as possible to avoid oxygen limitation in the experiments. 4.3 Experiment 3 - Oxygen dependence Purpose To try to find a way to interpret the experimental data from the experiments acetate was added as a carbon source to the experimental set up of the next experiment. Acetate is a carbon source the microorganisms can utilize directly, and it was added in a high concentration creating a surplus of carbon. Both acetate and oxygen is transported to the microorganisms by diffusing into the biofilm and when the acetate is in surplus the access oxygen becomes limiting. A parallel reactor containing unfiltered inlet water was also included in order to put the OUR from the acetate reactor into perspective with something that is similar to the previous experiments. The goal of the experiment was to find a relationship that can be used to describe the oxygen limitation. A reflection from experiment 2 was that the aeration intensity is important for the comparability of OUR between two reactors. To achieve the same level of oxygen in both reactors a flow meter was to be used to adjust the flow of air to the same intensity. Another reflection was that the aerated time interval was too short during experiment 2, thus needed to be prolonged to give the oxygen level in the reactor enough time to reach its maximum again after the unaerated periods Expected results The OUR graph of acetate was expected to be constant, where the oxygen consumption rate is constant until the acetate is totally consumed. An estimation of how large the active biomass is could be made from the results of this experiment. A problem could arise if the acetate concentration chosen increases the microbial consumption of oxygen to such an extent that the oxygen concentration quickly reaches zero during the unaerated intervals. To prevent this from occurring either the concentration of acetate can be lowered or the biomass can be reduced, lowering the activity in the reactor Changes to setup The reactors in this experiment contained the following carbon sources: Reactor 3A - 85 mg acetate Reactor 3B l unfiltered inlet water 20

33 The aeration in the two reactors was measured with a flow meter and the flows were adjusted to the same intensity before the experiment started. The aeration was calibrated using flow meters and rotameters to set the initial air flow to 2.5 l/min in each reactor. The time intervals of aeration were prolonged from the ones used in experiment 2. A timer was used to start and stop the aeration Procedure 1 l outlet water was used as bulk liquid during the pre-period in the two reactors. A highly concentrated acetate solution had been prepared in advance. The strong concentration prevents degradation by microorganisms as well as reduces the volume that has to be added to the reactors. On the day of the experiment the acetate solution was diluted with water before it was added to the reactor. The reactor contained 85 mg/l acetate after the addition. The timer was set to intervals of 13 minutes and 15 seconds aeration, followed by a 5 minutes and 50 seconds long unaerated period. The experiment was run for a total of 4 hours. 50 K3 carriers were placed in each reactor and then the outlet water was added. The first hour was a pre-period, where 1 liter of outlet water was used. After the pre-period, 500 ml was removed from each reactor and 500 ml of the solution containing the carbon source was added. Samples of the reactor bulk were taken every half hour for measurements of VFA, starting after the addition of the carbon source. COD samples were taken as described in 3 Materials and methods Results from oxygen dependence experiment In Table 4.1 the results from the COD samples from the experiment are shown. Table 4.1: The COD measured on the raw water and before and after the experiment. Filtrated sample only contain dissolved particles smaller than 1.6 μm. In Figure 4.5 the oxygen levels in the reactors are presented. The oxygen level in the two reactors was not the same although the aeration was calibrated shortly before the experiment started, see Figure 4.5. The pre-period had a higher level than the postperiod, where the carbon source had been consumed, indicating that there was carbon that the microorganisms could utilize in the outlet water used as medium in the preperiod. The lengths of the descents of the oxygen concentration in Figure 4.5 were 21

34 longer after the addition of unfiltered inlet water. This could be explained by the variety of carbon sources that was included in raw wastewater which provides for a larger range of microorganisms. A bigger part of the biomass is active when for instance ethanol is present, because some bacteria that are unable to degrade acetate may utilize ethanol. The oxygen level in the acetate reactor didn t decrease as much as was presumed when planning the experiment. The narrow increase shortly before the fourth decent was due to the decreased volume when 500 ml of the outlet water in the preperiod was pumped out and the probe of the oxygen meter was out of the water for a short time period until the carbon source was added to the reactors. Figure 4.5: The oxygen concentration in the two reactors plotted against the time. The maximum oxygen uptake rate is presented in Figure 4.6. The fourth point in 3A is in the level of the OUR in the pre-period although the carbon source already was added. Perhaps it indicates that the addition was too close to the unaerated period. From the fifth point and on in Figure 4.6, the OUR in the acetate reactor was constant at an elevated level until the acetate had been consumed. This result is comparable to similar experiments conducted with acetate in activated sludge (Hagman & la Cour Jansen, 2007). The fourth point of the unfiltered inlet water series was very high compared to the other points, probably due to the fact that there were numerous easily degradable organic compounds in the raw wastewater. Ethanol can for instance be degraded by microorganisms that don t use acetate as a substrate and therefore a larger fraction of the biomass present in the reactor was active and the OUR became very high during the first minutes. After that the OUR in 3B quickly decreased to close to pre-period levels, however since they were elevated they give a false impression of the amount of time it took to consume the inlet water. The use of outlet water in the pre-period seems to have cause problems in the method by adding a carbon source to the microorganisms in the pre-period. 22

35 Figure 4.6: The maximum OUR in the two reactors plotted against time. The pre-periods in Figure 4.6 were not on the same level despite the fact that the oxygen level, bulk liquid and biomass should be identical. One or several of these factors must have differed between the reactors. The oxygen level was clearly not equal in the two reactors but that does not exclude that other errors occurred as well. Oxygen dependence In Figure 4.7 and Figure 4.8 the OUR is plotted against the oxygen concentration in each decent to see if a relationship between the parameters could be found. The descents are numbered from 1 to 13 in both reactors. The carbon sources were added before the fourth unaerated interval. In the acetate reactor, Figure 4.7, the 5 th 7 th unaerated periods tend to have larger OUR than the other intervals. However, according to Table 4.2, which shows the slopes of the linear descents in Figure 4.7, there was not a clear oxygen dependence during the degradation of the acetate in this experiment. Table 4.2: Slope of the trends in OUR during consumption of external carbon in reactor 3A. Figure 4.7: The OUR in the acetate reactor is plotted against the oxygen concentration. The legend shows which of the unaerated periods that is plotted. 23

36 In Figure 4.8 the unaerated periods from the unfiltered reactor is plotted against the oxygen concentration and there is a linear relationship between the OUR and the oxygen concentration during descent number 4 and 5, see Table 4.3. After that the OUR was very similar to the pre- and post-periods where there was no COD in the reactor. The COD added to the reactor seems to have been small because it was quickly consumed, only two descents, 4 and 5, have an elevated OUR value. There seems to have been a shift from an initially high oxygen dependence in descent number 4 to a significantly lower dependence in number 5. It would indicate stronger oxygen dependence while the surplus of acetate was large in the beginning of the experiment, which is consistent with the theory of carbon and oxygen dependence. Table 4.3: Slope of the trends in OUR during consumption of external carbon in reactor 3A. Figure 4.8: The OUR in the unfiltered reactor is plotted against the oxygen concentration. The numbers define which of the unaerated periods that is plotted Summary of experiment 3 The OUR in the acetate reactor showed similarities to comparable experiments using activated sludge. The oxygen dependence was clearer in the unfiltered reactor than in the acetate reactor. In the unfiltered reactor the oxygen dependence was larger when a carbon source was present, indicating an oxygen limited process, whereas the other intervals was limited by carbon supply. Improved aeration is essential to the method development, to make it possible to compare reactors to each other, and must be further developed. To do this the calibration of the aeration must be further developed. The diffuser stones must distribute equal air bubbles. The outlet water most definitely contained carbon in this experiment because the pre-period had a higher oxygen level than the post-period. Water would be a more appropriate pre-period medium, where only the carbon in the biofilm would affect the oxygen level before the carbon source is added. The biomass should be evenly distributed between the two reactors and statistically the probability of identical biomass in both reactors increase if the carriers are collected from the pilot by the same person and directly placed into a plastic box intended for each reactor. 24

37 The time used for the aerated intervals was sufficient for the reactor using unfiltered wastewater, but too long for the acetate reactor which was aerated faster. 4.4 Experiment 4 - Repeatability test Purpose The purpose of this experiment was to test the repeatability of the experimental work. By adding equal amounts of the same substrate to two reactors run in parallel, the possibility to achieve the same OUR in the reactors was investigated. Further, changes in the performance of the biomass on the carriers could be studied by running the experiment twice. In order to limit the influence of the oxygen concentration, the same oxygen level was to be kept in the reactors. Also, the reactors had to be set up the same way and in order to ensure the reliability of the data, close to equally calibrated oxygen meters were to be used Expected results The OUR was expected to be the same in the two reactors during both the first and second run. However, the performance of the biomass and subsequently the OUR was expected to be higher in the first run than in the second one. In terms of oxygen concentration, the same level was expected in the reactors during both runs Changes to setup Based on the results from experiment 3 shown in Figure 4.5, it was clear that shorter aerated intervals could be used. 9 minutes of aeration was found to be sufficient and subsequently the aerated intervals were reduced from 14 to 9 minutes. Two pairs of reactors were run and they all utilized 85 mg of acetate as carbon source. The ones in the first run are denominated 4A and 4B, while those in the second run are denominated 4C and 4D. Only one flow meter was available, thus it was swapped between the reactors when adjusting the aeration Procedure 200 carriers were collected at Kävlinge and brought back to the laboratory. Unlike in experiment 1 and 2, the carriers were collected in separate containers - 50 in each. Thereby, four batches with a similar composition of biomass were achieved. However, there was a leakage of water from one of the boxes holding carriers during the trip from the pilot plant. Together with carriers from one of the other boxes, the ones in the box with the leakage were used for adjustment of the aeration equipment - pumps, diffusers and rotameters. Half of the carriers in each box were used in one reactor, while the other half was used in the other. Further, different Oxygen meters were tested until two close to equally calibrated ones were found, see Appendix D. When the aeration equipment had been adjusted to a satisfactory level, the flow of air to both reactors was about 2 l/min. This flow was maintained throughout the entire experiment. Subsequent to the adjustment of the aeration equipment, the carriers in the reactors were replaced with new ones. The carriers in the first of the two remaining boxes were 25

38 added to one reactor and the ones in the second box were added to the other reactor. 1 l of tap water was then added to each reactor and a pre-period of about 40 minutes was run. 5 ml from a 17 g/l acetate stock solution was then added to the reactors from a bulk solution that had been prepared prior to the experiment and the experiment continued for another hour. After the first run, the reactors were emptied of water and then swapped places with each other. The aeration equipment and oxygen meter used in 4A during the first run was thereby used in 4D during the second run and, conversely, the same aeration equipment and Oxygen meter was used in 4B and 4C. 1 l of tap water was then added to each reactor and a second pre-period of 45 minutes was run. After addition of 5 ml from the 17 g/l acetate stock solution to the reactors, the experiment was run for another 1.5 hours Results from the repeatability experiment Variations in the oxygen concentration in reactor 4A and 4B during the experiment are presented in Figure 4.9. There was a clear difference in oxygen concentration between the reactors, which is explained partly by differences in the calibration of the meters, see Appendix D. The differences in oxygen concentration were however too great to be explained solely by the calibration. It seems like the oxygenation of reactor 4A was better than that of 4B throughout the entire experiment. Figure 4.9: The oxygen concentration as a function of time in 4A and 4B using 85 of mg acetate. Figure 4.10, in which the oxygen concentration in 4C and 4D is shown, indicates a smaller difference between the reactors in the second run than in the first. This is explained partly by the swap of the reactors in between the first and second run. Due to unequal calibration of the oxygen meters, the difference in oxygen level between the reactors was amplified during the first run, see Figure 4.9. During the second run, on the other hand, the difference was impaired as the better aeration equipment was used in 4C. The actual difference in oxygen level between 4C and 4D is thereby not obvious in Figure

39 Figure 4.10: The oxygen concentration as a function of time in 4C-D. Interestingly, the flow meters showed no significant changes in the aeration of the reactors during the experiment. This suggests the biomass in 4A and later 4D was more active than that in the other reactors. OUR Figure 4.11 presents the maximum OUR in 4A and 4B throughout the experiment and as seen the trends in the two reactors are similar. The seventh data point is however higher in 4A than in 4B. As seen in Figure 4.9, more oxygen was consumed in 4A during the seventh descent even though equal amounts of COD were added to 4A and 4B, see Appendix B. This could be due to that the microbial activity in 4A and 4D was higher than that in the other reactors. Figure 4.11: The maximum OUR as a function of time in 4A-B. The maximum OUR in reactor 4C and 4D is shown in Figure 4.12 and, as seen in the figure, oxygen was consumed to the greatest extent in 4D. 27

40 Figure 4.12: The maximum OUR as a function of time in 4C-D. Based on the results shown in Figure 4.12, it is apparent there were differences either in the oxygenation or in the microbial activity, most likely in both, between 4C and 4D. Furthermore, the OUR in the oxygen span 6-7 mg O2/l was determined and the results are presented in Figure 4.13 and Figure Figure 4.13: The OUR as a function of time in 4A-B in the span 6-7 mg O2/l. Except for the fifth data point, the OUR in 4A and 4B follows the same pattern in the interval 6-7 mg O2/l as when the maximum OUR was found. The same accounts for 4C and 4D, in which the trends in OUR were unchanged when the oxygen span 6-7 mg O2/l was studied. 28

41 Figure 4.14: The OUR as a function of time in 4C-D in the span 6-7 mg O2/l. Based on the maximum OUR, the oxygen consumption was found to be higher in 4A than in 4B. When the calculations were based on the OUR calculated in the interval 6-7 mg O2/l, on the other hand, the oxygen consumption was close to the same in both reactors. Further, the oxygen consumption in 4C was also almost equal to that in 4A and 4B. This clearly demonstrates the importance of achieving equal aeration in two reactors run in parallel. All numbers on the oxygen consumption are found in Appendix C. Oxygen dependence Figure 4.15 shows the oxygen dependence in 4A and Table 4.4 shows the slope of the trends in OUR during consumption of external carbon in the reactor. According to the table, there was no clear trend in the oxygen dependence during the consumption of external carbon. Table 4.4: Slope of the trends in OUR during consumption of external carbon in reactor 4A. Figure 4.15: OUR as a function of the oxygen concentration during all descents in reactor 4A. 29

42 Figure 4.16 shows the oxygen dependence in 4B and Table 4.5 shows the slope of the trends in OUR during consumption of external carbon in the reactor. Based on the calculated slopes, there were no clear trends in the oxygen dependence in reactor 4B. The oxygen dependence was however stronger in 4B than in 4A, perhaps as a result of unequal aeration of the reactors. Table 4.5: Slope of the trends in OUR during consumption of external carbon in reactor 4B. Figure 4.16: OUR as a function of the oxygen concentration during all descents in reactor 4B. Figure 4.17 and Figure 4.18 show the OUR as a function of the oxygen concentration in reactor 4C and 4D, respectively. Table 4.6 and Table 4.7 show the oxygen dependence during the consumption of external carbon in the reactors. Table 4.6: Slope of the trends in OUR during consumption of external carbon in reactor 4C. Figure 4.17: OUR as a function of the oxygen concentration during all descents in reactor 4C. There was no clear difference between 4C and 4D regarding the oxygen dependence during the consumption. In comparison with reactor 4A and 4B, however, there was generally a lower oxygen dependence in 4D and possibly also in 4C. 30

43 Table 4.7: Slope of the trends in OUR during consumption of external carbon in reactor 4D. Figure 4.18: OUR as a function of the oxygen concentration during all descents in reactor 4D Summary of experiment 4 It can be concluded that the reactors in pair is similar but that further development is needed to make the result fully comparable. Even more equal oxygen meters must be found and tested and the aeration must be equal in both reactors before the experiment starts. 4.5 Experiment 5 - Hydrolysis experiment Purpose This experiment aimed at testing the applicability of the methodology that was developed by experiment 1-4. Thus, results mainly from this experiment but partly also from experiment 3 and 4 will be used for evaluation of the methodology. Four waters with COD from different size fractions were to be characterized by the extent to which hydrolysis and subsequent microbial respiration of particles took place. In addition to testing the method, the experiment would thereby also increase the knowledge on the impact of COD from different size fractions on the hydrolysis taking place in an MBBR process Expected results The oxygen consumption was expected to be the highest in the unfiltered reactor. The sedimented reactor was expected be the second highest and the filtrated to have the lowest oxygen consumption of the reactors using wastewater. Hydrolysis is expected to be measurable in the unfiltered reactor by comparison to the filtered. 31

44 4.5.3 Changes to setup No changes were made to the setup used in experiment 4 and the following carbon sources were utilized: Reactor 5A - 85 mg of acetate Reactor 5B l of filtered inlet water from the pilot plant Reactor 5C l of unfiltered inlet water from the pilot plant Reactor 5D l of sedimented inlet water from the pilot plant 5A and 5B contained the least COD and were therefore run in parallel. 5C and 5D, which contained more COD, were subsequently run in parallel Procedure 200 carriers and 4 l of inlet water were collected at Kävlinge by and brought back to the laboratory. Like in experiment 4, the carriers were collected in separate containers - 50 in each. Before commencing the experiment, two equally calibrated oxygen meters were found, see Appendix D, and the aeration equipment was adjusted the same way as in experiment 4 so that an air flow of 2 l/min was achieved. The reactors where then filled with 1 l of tap water and one box of carriers was added to each reactor. By adding the carriers after the water, unnecessary physical stress to the carriers prior to starting the experiment was avoided. The agitation was then started carefully and a pre-period of almost one hour was run. When the pre-period ended, 250 ml of water was removed from each reactor and 5 ml from a 17 g/l acetate stock solution was added to reactor 5A together with 250 ml of tap water, while 250 ml of filtered inlet water was added to reactor 5B. The experiment then continued for about 1.5 hours. At the end of the run, the flow of air from the pump used to aerate reactor 5B had decreased to 1.4 l/min. Nothing was done about this. After the first run, the reactors were emptied and once again 1 l of tap water and one box of carriers was added to each reactor. A one hour long pre-period was then run, followed by removal of 250 ml of water from each reactor. Subsequent to the pre-period, 250 ml of unfiltered inlet water was added to reactor 5C and 250 ml of water from a 1 l bottle of inlet water, in which the particles had sedimented for 4 hours, was added to reactor 5D. After addition of external carbon, the experiment was run for 1 hour and 45 minutes longer Results from the repeatability experiment Figure 4.19 shows how the oxygen concentration in reactor 5A and 5B changed throughout the experiment. The oxygen concentration in both reactors varied within the same interval during the entire pre-period, thus equal amounts of air was supplied initially. After addition of carbon, the oxygen concentration dropped in both reactors as a result of the excess of easily accessible carbon. Surprisingly, the oxygen concentration reached a lower level in 5B than in 5A during the first descent seen in Figure Possibly, the biofilm in 5A was not accustomed to acetate before the addition. 32

45 Figure 4.19: The oxygen concentration in reactor 5A and 5B. Already during the second descent after addition of carbon, it is evident 5B contained the least fraction of easily accessible carbon. According to Figure 4.19, the oxygen consumption in the reactor decreased gradually and after about 45 minutes from the moment carbon was added to the reactors, the oxygen concentration reached the same level as during the pre-period. It is uncertain, however, to which level the oxygen concentration dropped during the third descent. The oxygen meter used to measure the oxygen concentration in 5B was subject to a battery malfunction during the unaerated interval, thus data from part of the third descent is missing. Possibly, most of the easily accessible carbon in 5B was consumed already within 30 minutes. In contrast to 5B, 5A experienced relatively constant oxygen consumption for 45 minutes and then suddenly the oxygen concentration reached the same level as prior to the addition of carbon. Figure 4.20: The oxygen concentration as a function of time in reactor 5C and 5D. Figure 4.20 shows the trends in oxygen concentration in 5C and 5D and the results indicate that less air was supplied to 5C than to 5D. Subsequently, the oxygen 33

46 concentration increased at a slower rate in 5C. Possibly a change in the settings of the rotameter used to regulate the flow of air to 5C during the experiment explains this. Also, the difference in oxygen level between 5C and 5D was greater than between 5A and 5B. The reason for this is unknown. The respiration in 5C and 5D returned to the level of endogenous respiration after about one hour from the moment carbon was added. Further, the trends in oxygen concentration as well as the length of the descents were quite the same in both reactors during the run. This implies that the extent, to which oxygen was consumed in 5C and 5D, was also quite the same. OUR As seen in Figure 4.21, after addition of external carbon the OUR in 5A was constant at an elevated level for 45 minutes and then decreased instantaneously while it decreased gradually in 5B. Figure 4.21: The OUR as a function of time in reactor 5A and 5B. Figure 4.22 shows how the OUR changes throughout the second run, in which unfiltered and sedimented inlet water from the pilot plant were used as carbon sources. Like the differences in oxygen concentration between 5C and 5D, the differences in OUR between the reactors are probably due to a combination of uneven aeration of the reactors and differences in the composition of the COD. However, during the first 30 minutes after addition of carbon to the reactors, the OUR was clearly higher in 5C than in 5D. This could be explained by hydrolysis, but also by differences between the reactors regarding the amount of dissolved COD, see Appendix B. 34

47 Figure 4.22: The OUR as a function of time in reactor 5C and 5D. According to calculations of the oxygen consumption, close to twice the amount of oxygen consumed in 5B was consumed in 5A. About 30 % more oxygen was consumed in 5C than in 5D according to calculations. All numbers on the oxygen consumption are found in Appendix C. Oxygen dependence Figure 4.23 shows how the OUR in 5A varied with the oxygen concentration in the reactor during the experiment and Table 4.8 shows the slopes of the trends. During consumption of the easily accessible acetate, the OUR was clearly dependent on the oxygen concentration in the reactor. Furthermore, the oxygen dependence increased gradually during the fourth, fifth and seventh descent. According to Table 4.8, the oxygen dependence during consumption of acetate peaked during the seventh descent. Table 4.8: Slope of the trends in OUR during consumption of external carbon in reactor 5A. Figure 4.23: OUR as a function of the oxygen concentration during all descents in reactor 5A. 35

48 According to Figure 4.24 and Table 4.9, the OUR in 5B was most dependent on the oxygen level during the fourth and fifth descent. Like in 5A, the oxygen dependence in 5B increased gradually after addition of external carbon and it peaked during the fifth descent. Further, comparison of the results in Table 4.8 with those in Table 4.9 reveals a significantly stronger oxygen dependency during consumption of acetate than during consumption of filtered inlet water from the pilot plant. Table 4.9: Slope of the trends in OUR during consumption of external carbon in reactor 5B. Figure 4.24: OUR as a function of the oxygen concentration during all descents in reactor 5B. Figure 4.25 shows the OUR in 5C as a function of the oxygen level in the reactor during the experiment and Table 4.10 shows the slopes of the trends. The microbial activity in 5C was most limited by the availability of oxygen during the fifth and sixth descent. Also, the oxygen dependency in 5C is more apparent than that in both 5A and 5B, as seen in Table Table 4.10: Slope of the trends in OUR during consumption of external carbon in reactor 5C. Figure 4.25: OUR as a function of the oxygen concentration during all descents in reactor 5C. Figure 4.26 shows how the OUR in 5D varied with the oxygen level in the reactor during the experiment. The biomass was clearly limited by the amount of oxygen in the 36

49 reactor during the fifth and sixth descent, as seen in Table It seems like the respiration in 5D was less dependent on the oxygen level than that in 5C. This suggests the unfiltered inlet water perhaps contained more readily available carbon than the sedimented water. Table 4.11: Slope of the trends in OUR during consumption of external carbon in reactor 5D. Figure 4.26: OUR as a function of the oxygen concentration during all descents in reactor 5D Summary of experiment 5 Even though the COD content in reactor 5B was higher than that in 5C, the oxygen consumption was the highest in 5C, see Appendix B and Appendix C. This supports that hydrolysis of particulate COD occurred in 5C. The baselines representing the endogenous respiration are not the same in all reactors, despite the efforts in handling the biofilm in all reactors identically. This suggests that the conditions for the biofilm in the different reactors were not identical, as desired. Too rough aeration causes sloughing of biomass from the carriers and thereby affects the performance of the biofilm. The oxygen dependence increased with increasing amount of readily accessible carbon in the reactors. As seen in Appendix C, different oxygen consumption was the result of addition of COD from different size fractions. 4.6 Evaluation of the method In experiment 5 the oxygen consumption is larger in the unfiltered sample compared to the filtrated sample despite the fact that the dissolved COD is higher in the filtrated sample. The most probable explanation for this is that the particles in the unfiltered wastewater have been hydrolyzed to small enough fragments to be utilized by the microorganisms. This result show that it is possible to measure hydrolysis using the OUR method. However, hydrolysis of particles that results in larger fragments than the microorganisms can use will not be measured by this method. To utilize the full potential of the methodology developed, it is important to consider several aspects. This following discussion covers the ones identified as most important in experiment 1 to 5. 37

50 Oxygenation is the single most important factor. It contributes to the turbulence mixing the carriers vertically in the reactor. In terms of comparability, equal aeration of reactors run in parallel is desired since the methodology is based on the study of differences in OUR and oxygen consumption, which both are strongly correlated to the oxygen level in the reactor. Further, convection increases the extent to which organic particles are hydrolyzed by transporting particles from the bulk liquid to the biofilm surface and by thinning out the stagnant layer just outside the biofilm surface. Too rough agitation in the laboratory scale reactors causes sloughing of biomass from the carriers, thus the agitation intensity must be kept at a moderate level. It is also important to achieve a high oxygen level in the reactors during the experiments due to the oxygen limitation in the biofilm. In experiment 4 it is shown that the oxygen dependence is lower when the oxygen level is high in the reactor. The OUR should to the greatest extent possible be calculated in the same oxygen interval when comparing results between reactors due to the clear oxygen dependence in the MBBR carrier process. In order to reach the microorganisms in the biofilm, the oxygen has to diffuse into the biofilm. Otherwise it is hard to isolate the dependence of carbon in the biofilm and accurately determine the hydrolysis. In experiment 4 it is shown that the oxygen consumption from reactors with the same content are more similar when the values are calculated in the same oxygen interval, see Appendix C. Further, the calculations of the oxygen consumption during the experiments are based on a quite uncertain assumption, which is that each calculated OUR in the experiments is constant for a certain period of time. In reality, it is unknown how the OUR varies between the data points in the OUR graphs presented in this report. To ensure that the quality of the biofilm as well as that an equal amount of biofilm, and thereby the same microbial activity, is achieved in reactors run in parallel, it is important to collect the carriers carefully and to treat them all in the same way throughout the entire handling. The carriers are sampled from the pilot tank by the same person and put into separate containers, collecting the same number as the number of reactors used in the experiment. Thereby, as all batches of carriers are handled the same way, differences between biomass in the reactors due to the human equation are minimized. Also, the statistical probability of equal biomass increases when the carriers are sampled from a large container and put directly into the reactor. Furthermore, the agitation of the reactors is started gently in order avoid initial sloughing of biomass from the carrier surface. The biofilm is always subject to friction due to the carriers collide with each other, the wall of the reactors, the aeration equipment and with the probe of the oxygen meter. During storage of wastewater samples, some COD is always consumed by suspended bacteria in the water. All reactors in the experiment should therefore preferably be run simultaneously. By filtrating the wastewater samples used in the experiment shortly 38

51 after sampling, suspended bacteria are removed from the water and the consumption of COD prior to use in the experiment is reduced. However, unless all wastewater samples used in the experiment is filtrated there will be unequal conditions in the samples. This is due to the degradation of COD in unfiltered wastewater that also leads to a lowered oxygen level whereas filtration in addition to lowering the microbial activity in the wastewater samples, also increases the oxygen level in the sample by allowing oxygen to diffuse into the water. The level of endogenous respiration is of great importance in the calculations of the oxygen consumption in the experiments. Accurate determination of the level of endogenous respiration increases the reliability of the results. This could be achieved by increasing the length of the pre-period, thus allowing the biofilm to consume more of the readily degradable carbon that comes with the carriers when they are collected. Another approach is to put the carriers in oxygenated tap water for a few hours before and then when the experiment starts the carriers are transferred to the reactors. Procedures to lower the carbon content in the biofilm prior to starting the experiment are relevant particularly when the wastewater has a high carbon content. The level of endogenous respiration could possibly also be determined at the end of the experiment by extending the time the experiment is continued after external carbon has been consumed. 39

52

53 5 Hydrolysis experiments 5.1 Experiment 6 - Significance of particles Purpose If the extent to which particles in wastewater are hydrolyzed is dependent on the concentration of particles, measurable differences in OUR between wastewaters with different particle content will possibly be observed. In this experiment, three wastewaters with particles from 2, 1 and 0.5, l of wastewater were produced and investigated. The aim was to determine whether the OUR increases with particle content Expected results A higher particle concentration is believed to lead to an increased hydrolysis of particles in wastewater. If that is wrong, there will be no distinction between the three reactors that can be explained as an increased hydrolysis Changes to setup Three reactors were run in parallel instead of two, as described in Materials and methods, and they contained the following carbon sources: Reactor 6A ml of tap water and particles from 2 l inlet water Reactor 6B ml of tap water and particles from 1 l inlet water Reactor 6C ml of tap water and particles from 0.5 l inlet water Procedure 5 l of influent wastewater and 200 carriers was collected at Kävlinge and brought back to the laboratory. The carriers were kept in four plastic containers with effluent wastewater - 50 in each container. Back at the laboratory, the particles in a total of 3.5 l of inlet water were separated from the water through filtering. About 125 ml of inlet water was filtered through each filter. The particles were then gently washed off the filters with tap water into glass beakers. Three beakers were used since three separate bulk solutions with particle contents corresponding to 0.5, 1 and 2 l inlet water were desired. About 300 ml of tap water was needed to wash off all the filters that the filtering of 2 l of inlet water generated. The bulk solutions based on 0.5 and 1 l of inlet water were therefore each diluted to a volume of 300 ml. While filtering the inlet water, one single reactor holding 1 l of tap water and 50 carriers was used to adjust the air flow from the three pumps that were to be used in the experiment. When the air flow had reached a satisfactory level, a pre-period with the three parallel reactors that were to be used in the experiment was run. 1 l of tap water and 50 carriers were used in each reactor during the pre-period as well. Since the filtering required an additional 1.5 hour after the air flow had been adjusted, a 1.5 hour long pre-period was run. 41

54 Once the filtering was finished, 300 ml of water was removed from each of the reactors and the carbon sources were added. The experiment was then run for an additional 4 hours Results from the investigation of particles significance Figure 5.1 shows how the oxygen concentration in the three reactors varies during the 6 hours long experiment. The low oxygen levels in reactor 6C are due to low capacity of the pump used to aerate the reactor. In order to increase the oxygen level in the reactor, the pump was replaced with a better one. This was done during the second aerated interval of the pre-period, thus about half an hour after the initiation of the preperiod. It was however not possible to reach the same air flow to 6C as to the other reactors, which is clearly seen in the figure. Figure 5.1: Oxygen concentration in the three reactors as a function of time. Figure 5.2 shows the OUR in the reactors that was calculated from the descents in Figure 5.1. The OUR was very high in the beginning of the pre-period, only to decrease to the base level of endogenous respiration after about 30 minutes. This is explained by the high content of COD in the outlet water in the pilot tank due to the high retention time during the sampling, see Appendix B. Although the carriers are placed in tap water there is carbon in the biofilm that are consumed during the first minutes of the pre-period. However after the carbon is consumed the OUR decreases to pre-period levels. 42

55 Figure 5.2: OUR at the three different particle concentrations as a function of time. Reactor 6C shows a significantly higher OUR at the third data point in Figure 5.2 than the other two reactors. This is probably due to the oxygen deficiency and subsequent constrained microbial activity in 6C during the first 30 minutes of the experiment, caused by the insufficient aeration of the reactor. With equal aeration in all three reactors, the trends in OUR during the pre-period would probably have been more the same. After the addition of carbon source to the reactors, the OUR stays higher in 6A than in 6B and 6C until almost 3.5 hours of the experiment has passed. When the filters were washed, some dissolved COD came with the particles, thus dissolved COD was added to all three reactors together with particles. The bulk solution containing particles from 2 l of inlet water contained most dissolved COD, most likely since it required most filters for preparation, while the bulk solution with particles from 0.5 l of water contained the least, see Appendix B. Thus, more dissolved COD was probably added to reactor 6A than to the two other reactors Summary of experiment 6 The OUR was clearly higher in 6A and this could be explained either by an increased level of soluble COD or by the fact that the addition of more particles contributed with a larger amount of easily degradable substrates. There was no apparent difference between 6B and 6C. These observations supports that the hydrolysis of particles in the wastewater is unaffected by the amount of particles present. 43

56 5.2 Experiment 7 - Influence of dissolved carbon Purpose The importance of dissolved organic matter for the hydrolysis of particles is to be examined in this experiment. The hypothesis is that dissolved COD will prevent hydrolysis from happening, and that less hydrolysis will be observed when more dissolved COD is added Changes to setup The same setup as in experiment 5 was used and the reactors were run with the following carbon sources: Reactor 7A ml of filtered inlet water Reactor 7B ml of filtered inlet water and particles from 1 l inlet water Reactor 7C ml filtered inlet water and 60 mg of acetate Reactor 7D ml filtered inlet water, particles from 1 l of inlet water and 60 mg of acetate Furthermore the reactors were run in pairs, first 7A-7B and then 7C-7D Procedure Theory Amount of particles Experiment 6 was used as an estimation of how much particles should be added to the reactors. The minimum amount that needs to be added is particles from 0.5 l of inlet water according to calculations performed. Because 2 l would take too long time to filtrate, we chose to add particles from 1 l filtrated inlet water. Amount of dissolved COD To estimate the amount of dissolved COD to add to the reactors, experiment 5 was used as template. In experiment 5 the following times can be deducted from the input of carbon source to the point in time where the activity is no longer detectable with the OUR method: 250 ml filtered inlet water 45 minutes 250 ml unfiltered inlet water 45 minutes 85 mg acetate 1 hour The experiment must keep to a total length of three to four hours including the preperiod. The combination of carbon sources that is most time consuming is reactor 7D, in which particles, filtered inlet water and acetate are mixed. If 250 ml filtrated inlet water, 60 mg/l acetate and particles from 1 l filtrated inlet water is added, the experiment must run for two hours after the addition of carbon source. 44

57 Practical 6 l of influent wastewater and 200 carriers was collected at Kävlinge and brought back to the laboratory. The carriers were kept in four plastic containers with effluent wastewater - 50 in each container. According to measurements, the inflow to the pilot plant was the same as in the previous experiment (0.3 l/s). Back at the laboratory, the particles in a total of 2 l of inlet water were separated from the water. The same filtering and washing procedures as described in Experiment 6 were applied and two bulk solutions, each with a particle content corresponding to 1 l of inlet water, were derived. About 250 ml of tap water was used to wash off all the filters that the filtering of 1 l of inlet water generated. 1 of the 2 l of filtered inlet water was kept for the experiment. While filtering the inlet water, the first pre-period was run and as soon as the filtering of inlet water was completed (after about one hour), 500 ml of water was removed from reactor 7A and 7B and the carbon sources were added. The reactors were then run for almost two more hours. After the first pair of reactors finished, a new pre-period with the second pair of reactors was started and, like the first pre-period, it was run for about an hour. Once again, 500 ml of water was removed from each of the reactors and the carbon sources were added. The acetate was added as 5 ml of a 12 g/l acetate stock solution. The experiment (including pre-period) finished after 3.5 hours. The COD values are presented in Appendix B Results from the investigation of dissolved carbons influence The oxygen concentration during the experiment is presented in Figure 5.3 and Figure 5.4. The carbon sources were added after 0.8 hours in Figure 5.5 and Figure 5.6, which is marked in the graphs as a black vertical line. The increase in oxygen concentration shortly before the fourth interval was due to the extraction of water to make room for the carbon source. The procedure left the oxygen meter in the air for a few minutes, which is clearly seen in the graph. The aeration in the reactors was struggling to increase the oxygen concentration which can be explained by the elevated COD content in the outgoing water from the pilot tank that the biofilm was taken from, see the measurements of COD on the outlet water that were taken in connection with experiment 6 (Appendix B). The lengths of the descents in the pre-period in 7A and 7B, Figure 5.3, were almost as long as the descents which also show that there was an ongoing consumption although no carbon source was added. It could have been avoided by storing the biofilm carriers in tap water for an hour before the experiment, extending the pre-period or by increasing the residence time in the pilot tank. However it was not possible to use any of these methods due to the tight schedule. The total time for the experiment would have increased too much, and the pilot plant was adjusted for another experiment at the time of sampling. After the carbon source was consumed, the OUR returned to the level of the endogenous respiration that was used as the base line in calculations of the hydrolysis. The aeration was equal in the reactors which can be seen in the pre- and post-period, where the oxygen concentration was very similar. 45

58 Figure 5.3: The oxygen concentration in reactor 7A and 7B as a function of time. In Figure 5.4 the oxygen level is higher than in Figure 5.3 which is explained by the fact that the carriers for this experiment were stored during the time it took for reactor 7A and 7B to run, because the same equipment was used. This gave the biofilm more time to consume the carbon in the outlet water they were stored in and entered the preperiod with less carbon in the biofilm. The pre-period medium was tap water which was not contributing with any carbon, so the only carbon found in the pre-period was the one found in the biofilm itself. Figure 5.4: The oxygen concentration in reactor 7C and 7D as a function of time. In Figure 5.5 and Figure 5.6 the OUR in reactor 7A-B and 7C-D respectively is presented. The carbon in the outlet water can be seen in these graphs as well as that the OUR was initially higher during the pre-periods in both graphs. The OUR during the preperiod in 7C-D was lower than in 7A-B which supports the theory that some carbon in the biofilm was consumed before the pre-period was started due to the consumption during the wait. 46

59 Figure 5.5: The OUR-graph for reactor 7A and 7B. In Figure 5.5 the OUR exhibits a pattern well known from the previous experiment with a peak after the addition of carbon source and a diminishing OUR up to the base line was reached. It is interesting to see the difference between the OUR in 7A compared to 7B when all that differed was the added particle solution. It could be explained by the hydrolysis of the particles, which lead to a larger OUR in 7B. In Figure 5.6 the reactor containing particulates 7D shows a higher OUR than 7C indicating that the hydrolysis was contributing with an extra oxygen consumption in that reactor. It is not clear whether the soluble carbon added, acetate, had an impact on the hydrolysis, because the method needs further repetitive studies to ensure that quantitative analysis can be made using this method. However by the increasing OUR after the addition of carbon source it is a good assumption that the acetate was consumed first before the rest of the carbon sources was consumed. Figure 5.6: The OUR-graph for reactor 7C and 7D. 47

60 Hydrolysis There was a clear visible difference in OUR between the filtered reactor and the reactor with the particles in both cases, see Figure 5.5 and Figure 5.6. This could possibly be explained by a combination of two things, hydrolysis and a larger amount of dissolved COD in the reactors with the particles. The dissolved COD in the reactors was composed of an equal amount of filtrated inlet water in all reactors making up 106 mg/l in 7A, whereas in 7B the particles contributd with an additional 12 mg dissolved COD/l besides the substantial contribution in particulate COD, see Table 5.1 and Table 5.2. The acetate contributed with 60 mg dissolved COD/l in 7C and 7D and the particles contributed with 15 mg dissolved COD in 7D. To estimate the significance of the difference in dissolved COD of the hydrolysis seen in Figure 5.5 and Figure 5.6, a few assumptions were made. However, the assumptions must be used with caution in order to allow as accurate conclusions as possible to be drawn. Table 5.1: COD values of the inlet and outlet wastewater and of the particle solutions that was added to 7B and 7D in mg/l. Table 5.2: Dissolved COD in all reactors in mg/l. It was assumed that the 12 and 15 mg COD was made up of molecules that are easily accessible to the microorganisms and if they were consumed fully the oxygen consumption would be described by the equation below, where S is the overall consumption in the reactor giving the amount of oxygen consumed per added mg COD in the filtrated reactors during consumption of wastewater. The results are shown in Table 5.3. The difference in COD could explain at maximum 4 mg of the oxygen consumed in the 7B and 5 mg in 7D. This is to be compared to the difference in consumed oxygen the two reactor pairs of 6 mg O2 in 7A-B and 12 mg O2 in 7C-D, see Table 5.4. The COD difference could represent 65 % of the hydrolysis seen in Figure 5.5 and 45 % in Figure 5.6. That means that 35 % and 55 % respectively is demonstrated was due to hydrolysis. However, a repetitive experiment is needed to verify the finding and to quantify the numbers and the statistical uncertainty. Table 5.3: The difference in added carbon source between the filtered and reactor containing particulates is shown as COD and O2 in (mg/l). 48

61 In Table 5.4 the oxygen consumed in all reactors are also presented. The oxygen consumption was almost twice as large in 7C-D than in 7A-B and this is consistent with the fact that twice as much COD was added to 7C-D. This leads to the conclusion that the hydrolysis was not inhibited by the acetate. Table 5.4: The consumed oxygen in each reactor is presented in the middle column and the difference between the reactor pairs is shown in the last column Summary of experiment 7 Hydrolysis was detected both in 7B and 7D using the OUR-method. It can be concluded that the hydrolysis is not inhibited by the addition of an easily accessible carbon source because the difference in the oxygen consumed is larger rather than smaller as was expected should the hydrolysis be inhibited. 49

62

63 6 Discussion The findings in experiment 5 support the belief that hydrolysis may be detected with the methodology developed. The oxygen consumption in the unfiltered wastewater, 5C, was found to be higher than that in the filtrated, 5B, even though COD measurements demonstrated more dissolved COD was added to 5B than to 5C (145 mg COD/l versus 128 mg COD/l). It is therefore possible the difference in oxygen consumption between the reactors was the result of hydrolysis and consequently respiration of particulate COD. Possibly the explanation for the lower COD content in 5C is that the easily accessible COD in the reactor was subject to more extensive degradation by suspended biomass during the three hours storage than that in 5B, which was filtered and thereby free of microorganisms. To be able to compare the oxygen consumption between two reactors, it was found important to use OUR values based on the same oxygen concentration intervals in both reactors. Experiment 4, using the same acetate mixture in both reactors, the maximum OUR as well as the OUR in the interval 6 to 7 mg O2/l was determined, clearly demonstrated this. More air was supplied to 4A than to 4B, which resulted in a higher maximum OUR, calculated at the highest oxygen level, in 4A than 4B and consequently the oxygen consumption was higher in 4A than in 4B. On the other hand, when the OUR was calculated in the interval 6 to 7 mg O2/l in both reactors, there was no significant difference in the oxygen consumption between the reactors. The oxygen consumption in 4D was also close to equal to that in 4A and 4B. These findings proved that the single most important factor influencing the comparability of oxygen consumption and OUR values between reactors is the oxygen level. Thus, since the OUR values was calculated in the same oxygen interval in 5B and 5C, the observed differences in oxygen consumption were probably due to hydrolysis and not to differences in the oxygen concentration between the reactors. This further support the suggestion that hydrolysis was detected in experiment 5. The main argument against the conclusion that hydrolysis can be seen using the model described in this thesis is that the finding is not statistically verified by performing repetitive experiments proving that the result is analogous in more than one experiment. This is something that clearly needs to be further investigated to verify the results in this thesis. However, in experiment 7 it is demonstrated that in spite of a small increase in COD the reactor containing particulates compared to the filtrated reactor the hydrolysis is detectable both with and without acetate. The added acetate could not be proven to inhibit the hydrolysis, but further comparison of the results must await repetitive studies. Also, by taking further efforts to ensure important parameters, such as an equally high oxygen concentration in both reactors during the experiment and preventing sloughing of biomass out into the bulk liquid, the accuracy of the measurement can be 51

64 improved further. The oxygen level during the experiments is found to be the most important factor to be able to compare reactors against each other. Also the amount of suspended biomass in the bulk during the experiment should be minimized to isolate the hydrolysis performed by the biofilm, but since the biomass in the wastewater is removed by filtering the suspended biomass originates only from the biofilm sloughing that occurs during the experiment. It looks like the biofilm is exposed to rougher conditions in batch experiments than in the pilot. It is shown by the biomass that is sloughed from the carriers during the experiments. They are clearly covered in less biomass after four hours in the lab than after weeks in the pilot tank although the aeration is rougher there. 52

65 7 Conclusions The method developed was to be used to measure hydrolysis in an MBBR process using carriers by comparing the bacterial respiration rates in wastewater containing particulate organic matter and filtrated wastewater. The process is subject to oxygen limitation because the oxygen has to diffuse into the biofilm to reach the microorganisms and the oxygen level was identified as an important aspect when comparing reactors. Also the biofilm used in reactors run in parallel must be equal and to the greatest extent possible be preserved throughout the experiment. Taking these aspects into consideration, it is possible to detect hydrolysis in an MBBR carrier process using OUR methodology. After developing the method it was tested in two experiments investigating the shortterm influence of added particles on hydrolysis and whether hydrolysis is inhibited at shorter periods of time with elevated levels of dissolved carbon. The hydrolysis was found to be unaffected by the amount of particles in the wastewater and not to be inhibited at elevated concentrations of a readily available dissolved substrate. 53

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67 8 Suggestions for further research Before using the method developed to quantify hydrolysis of particles in an MBBR process, the reliability of the method should be statistically verified by repetitive experiments. A repetitive study using experiment 7 as a template is recommendable. The results can be used to statistically verify that hydrolysis can be detected by OUR methodology, but also to investigate whether the method can be used to quantify the hydrolysis it detects. If it is possible to quantify the hydrolysis, further studies of different operating conditions can be conducted. An interesting approach would be to find the amount of hydrolysis performed in an existing wastewater treatment process. It is possible to investigate the importance of substrate loading, temperature and residence time for any given wastewater. Further research could aim at mapping the relationship between hydrolysis in batch experiments and continuous systems. It would help applying the findings from studies on batch experiments to full scale continuous processes. An experiment similar to experiment 7, but using filtrated inlet wastewater instead of acetate would be interesting. It would help to further determine the relationship between the availability of easily accessible carbon and hydrolysis using a naturally occurring carbon source in wastewater treatment processes. 55

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69 9 References AnoxKaldnes. (2009, April). AnoxKaldnes MBBR - An overview of the technology. Lund. Boltz, J. P., & La Motta, E. J. (2007). Kinetics of Particulate Organic Matter Removal as a Response to Bioflocculation in Aerobic Biofilm Reactors. Water Environment Research: A Research Publication of the Water Environment Federation, 79 (7), pp Confer, D. R., & Logan, B. E. (1998). Location of Protein and Polysaccharide Hydrolytic Activity in Suspended and Biofilm Wastewater Cultures. Water Research, 32 (1), pp Dimock, R., & Morgenroth, E. (2006). The influence of particle size on microbial hydrolysis of protein particles in activated sludge. Water Research, 40 (10), pp Ellervik, U., & Sterner, O. (2007). Organisk Kemi (2nd edition). Lund: Studentlitteratur. Gillberg, L., Hansen, B., Karlsson, I., Nordström Enkel, A., & Pålsson, A. (2003). About Water Treatment. Helsingborg: Kemira Kemwater. Goel, R., Mino, T., Satoh, H., & Matsuo, T. (1999). Modeling Hydrolysis Processes Considering Intracellular Storage. Water Science and Technology, 39 (1), pp Hagman, M., & la Cour Jansen, J. (2007). Oxygen Uptake Rate Measurements for Application at Wastewater Treatment Plants. Vatten, 63, pp Haldane, G. M., & Logan, B. E. (1994). Molecular Size Distributions of a Macromolecular Polysaccharide (Dextran) During Its Biodegradation in Batch and Continuous Cultures. Water Research, 28 (9), pp Henze, M., Harremoës, P., la Cour Jansen, J., & Arvin, E. (1997). Wastewater Treatment (2nd ed.). Lyngby: Springer Verlag. Insel, G., Orhon, D., & Vanrolleghem, P. A. (2003). Identification and Modeling of Aerobic Hydrolysis - Application of Optimal Experimental Design. Journal of Chemical Technology and Biotechnology, 78 (4), pp Janning, K. F. (1998). Hydrolysis and oxidation of particulate organic matter in biofilters. Lyngby: Technical University of Denmark, Department of Environmental Science and Engineering. Janning, K., Mesterton, K., & Harremoës, P. (1997). Hydrolysis and Degradation of Filtrated Organic Particulates in a Biofilm Reactor under Anoxic and Aerobic Conditions. Water Science and Technology, 36 (1), pp Jonstrup, M., Murto, M., & Björnsson, L. (2010). Compendium in Environmental Biotechnology. Lund: Lunds Tekniska Högskola, Department of Biotechnology. Kommedal, R., Milferstedt, K., Bakke, R., & Morgenroth, E. (2006). Effects of initial molecular weight on removal rate of dextran in biofilms. Water Research, 40 (9), pp la Cour Jansen, J. (2011, February). Professor. Personal contact. Department of Chemical Engineering. Lund University, Lund. 57

70 La Motta, E. J., Jiménez, J. A., Josse, J. C., & Manrique, A. (2004). The Role of Bioflocculation on COD Removal in the Solids Contact Chamber of the TF/SC Process. Journal of Environmental Engineering, 130, pp La Motta, E. J., Jiménez, J. A., Parker, D., & McManis, K. (2003). Removal of Particulate COD by Bioflocculation in the Activated Sludge Process. Water Pollution VII; WIT Press, pp Larsen, T. A. (1992). Degradation of colloidal organic matter in biofilm reactors. Lyngby: Technical University of Denmark, Department of Environmental Engineering. Morgenroth, E., Kommedal, R., & Harremoës, P. (2002). Processes and Modeling of Hydrolysis of Particulate Organic Matter in Aerobic Wastewater Treatment - a review. Water Science and Technology, 45 (6), pp Okutman, D., Övez, S., & Orhon, D. (2001). Hydrolysis of settleable substrate in domestic sewage. Biotechnology letters, 23 (23), pp Priest, F. G. (1984). Extracellular enzymes. Van Nostrand Reinhold. Rohold, L., & Harremoës, P. (1993). Degradation of Non-diffusible Organic Matter in Biofilm Reactors. Water Research, 27 (9), pp United Nations, Dep. of Economic and Social Affairs. (2010, 11 10). United Nations: World Population Prospects, the 2008 Revision. Retrieved 12 31, 2010, from United Nations: (2010). World Health Statistics. World Health Organization. Ødegaard, H., Gisvold, B., & Strickland, J. (2000). The Influence of Carrier Size and Shape in The Moving Bed Biofilm Process. Water Science and Technology, 41 (4-5), pp

71 Appendix A - Reactor contents Table A.1: Reactor content in all experiments. I

72

73 Appendix B - COD measurements Table B.1: A compilation of all COD measurements that were taken in connection with the experiments. * - filtered sample. Table B.2: COD measurements on particle bulk solutions after filtration and before addition to the reactors. * - filtered sample. III

74

75 Appendix C - Oxygen consumption Table C.1: Oxygen consumption during all experiments. V

76

77 Appendix D - Test of oxygen meters In order to detect deviations resulting from the calibration of the oxygen meters used in experiment 4-7, the oxygen concentration in a water-filled vessel was measured with the oxygen meters used in parallel in each experiment. However, no test was carried out in connection with experiment 7 since the oxygen meters used in this experiment were tested already in connection with experiment 5. Meter 2 and 6, which were used in experiment 4, were tested in a beaker filled with tap water and the results from the measurements are found in Figure D.1. Figure D.1: Differences between the oxygen meters used in experiment 4 regarding measured oxygen concentration. On average, meter 2 measured a 0.26 mg O2/l higher oxygen concentration than meter 6. Two new oxygen meters were chosen for experiment 5 and they were tested in a reactor containing 1 l of tap water and 50 carriers. The results from the 1.5 hours long test are shown in Figure D.2. Figure D.2: Differences between the oxygen meters used in experiment 5 regarding measured oxygen concentration. VII

78 On average, meter 7 measured a 0.11 mg O2/l higher oxygen concentration than meter 8. Meter 6, 7 and 8 were used in experiment 6 and they were tested in a reactor holding 1 l of tap water and 50 carriers. Figure D.3 shows the results from the test. Figure D.3: Differences between the oxygen meters used in experiment 6 regarding measured oxygen concentration. According to the measurements, the average difference between meter 7 and 8 was 0.03 mg O2/l. The average difference between meter 6 and 7 was 0.23, thus the difference between meter 6 and 8 was The observations presented in this appendix clearly show the uncertainty associated with oxygen measurements. However, all deviations presented here are within or very close to the margin of error of the oxygen meters, which is 0.20 mg O2/l. VIII

79 Appendix E - TSS/VSS and VFA measurements Table E.1: TSS, VSS and flow measurements. Table E.2: VFA measurements, experiment 4. Table E.3: VFA measurements, experiment 5. IX