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Citation: von Sperling, M., Verbyla, M.E. and Mihelcic, J.R. 2018. Understanding Pathogen Reduction in Sanitation Systems: Units of Measurement, Expressing Changes in Concentrations, and Kinetics. In: J.B. Rose and B. JiménezCisneros, (eds) Global Water Pathogen Project. http://www.waterpathogens.org (J.R. Mihelcic and M.E. Verbyla) (eds) Part 4 Management Of Risk from Excreta and Wastewater) http://www.waterpathogens.org/book/understandingpathogenreductionsanitationsystemsunitsmeasurementexpressingchanges Michigan State University, E. Lansing, MI, UNESCO. Acknowledgements: K.R.L. Young, Project Design editor; Website Design: Agroknow (http://www.agroknow.com) 
Last published: July 27, 2018 
The purpose of this chapter is to provide readers of the individual chapters on onsite and sewered Sanitation System Technologies with background information so they may better understand: a) how pathogens are measured, b) how to express changes in pathogen concentrations, and c) how pathogen reduction (as covered here in the Sanitation Technologies chapters) relates to pathogen decay rates (as covered in the GWPP Persistence chapters) for sanitation technologies that are configured as batch or continuous flow systems with different degrees of mixing.
Pathogens in excreta and water are a diverse group of microorganisms that include from smallest size to largest, viruses, bacteria, protozoa, fungi, and the eggs of helminth worms. They are too small to see with the naked eye and are often present in low concentrations in water and biosolids. As such, there are several different ways pathogens are measured and enumerated in the laboratory. Each method has its own strengths and weaknesses. In fact, two different methods used to measure the same pathogen in the same sample may yield vastly different results! It is important for readers of these GWPP chapters to take this into consideration when interpreting data from the scientific literature.
The most common methods used to enumerate pathogens can be divided into three different classes: 1) culturebased methods, which measure the ability for pathogens to replicate and/or express certain enzymes in vitro, under specified laboratory conditions; 2) molecular and immunological methods, which involve the detection of specific antigens or segments of the pathogen’s genome; and 3) microscopybased methods, which require the laboratory technician to identify and count pathogen cells under a microscope (based on their physical characteristics). Sometimes, a combination of methods is used, such as immunofluorescence microscopy (combination of immunological and microscopybased methods) or integrated cell culture and polymerase chain reaction (culture and molecularbased method) for enumerating enteric viruses.
No single method is perfect. For molecular and immunological methods, the presence of a specific genome or antigen may indicate the presence of the pathogen, but does not necessarily confirm if the pathogen is viable or infectious. Also, with culturebased methods, some viable and infectious pathogens may not replicate or express enzymes in the laboratory, where conditions are not exactly the same as they are in the pathogen’s natural habitat (i.e., inside the host). Microscopybased methods are timeconsuming and require a trained microbiologist to identify pathogen species (which is not always possible as some pathogens are morphologically indistinguishable from other microorganisms). Tables 1a and 1b provide a summary of some common types of culturebased, molecular, immunological, and microscopybased methods used to enumerate pathogens, and show the units of expression that are associated with each method.
Units of concentration are simply reported as the unit of expression divided by some unit volume. By convention, this unit volume is most commonly 100 mL for bacteria, 1 L for viruses, and 1 L for protozoan parasites and helminth eggs.
There are several important terms that are used to describe changes in the measured concentrations of pathogens along the sanitation service chain. Removal refers to the physical elimination of pathogens from wastewater. Often, pathogens removed from wastewater are simply transferred to sludge, where they may remain viable. Inactivation refers to the physical destruction of pathogens resulting in a loss of viability—this can happen to pathogens in wastewater or in sludge. Growth refers to the replication of pathogens in a sanitation system. Some opportunistic, zoonotic, and bacterial pathogens are capable of regrowth within sanitation systems (Jjemba et al. 2010), but parasites and enteric viruses require a human host to replicate, and cannot regrow within sanitation systems. Pathogens may become volumetrically concentrated in smaller volumes of water or sludge due to evaporation or moisture removal (e.g. thickening, dewatering), which may cause the illusion of regrowth. To avoid this, pathogen concentrations in sludge can be expressed in terms of their number per dry mass instead of number per unit volume. In summary, pathogen concentrations in wastewater should be expressed as number per unit volume (typically per 100 mL for bacteria, per L for parasites and viruses, and sometimes per mL for viruses such as the coliphage). Pathogen concentrations in sludge or biomass should be expressed as number per unit dry mass (typically per g or kg for all pathogen types). Dry mass is sometimes reported by g TS, meaning grams of Total Solids, in the sense that the total solids analysis would give an indication of the dry matter present in the sludge or biomass.
The term reduction will be used throughout the sanitation technologies chapters to refer to the combined removal and inactivation of pathogens in wastewater systems. Unless stated otherwise, it is assumed that pathogen regrowth in sanitation systems is negligible. The efficiency of pathogen reduction in a particular sanitation system can be expressed as the percent (%) reduction efficiency. The percent reduction efficiency, E(%), is quantified as follows, where No is the influent pathogen concentration, and N is the effluent pathogen concentration (the units of concentration must be the same for N and No):
$$ E( \% ) = \frac{N_{0}  N}{N_{0}}\times100 \quad (1) $$
Pathogen concentrations are often discussed with respect to their order of magnitude, which is a way of comparing their relative size; in this context, base 10 comparisons are implied. For example, if one number is 10 (=10^{1}) times greater than another number, it is one order of magnitude greater. If a number is 1,000 (=10^{3}) times greater than another number, it is said to be 3 orders of magnitude greater.
In the case of pathogens and indicators of fecal contamination, the concentrations can be very high, and thus more attention is given to the order of magnitude of the concentrations instead of the absolute values themselves. For instance, a concentration of 183,098,765 MPN/100 mL is usually expressed as 1.83 × 10^{8} MPN/100 mL, giving more emphasis on the order of magnitude of 108 and recognizing that there is not much accuracy on the digits that come after 183.
Given these high numbers, another way of expressing this concentration is by taking the log_{10 }of the original value (this is known as the log_{10}transformed concentration). For instance, a concentration of 1.00 x 10^{8} MPN/100 mL has a logtransformed value of 8.00 (i.e. log_{10}(1.00 x 10^{8}) = 8.00). Likewise, 1.46 x 10^{8} MPN/100 mL has a logtransformed value of 8.16 (i.e. log_{10}(1.46 x 10^{8}) = 8.16).
An alternative to expressing pathogen reduction as a percentage is to use the log_{10} reduction value (LRV), which is defined as the difference between the logtransformed pathogen concentrations of the influent and effluent across a particular sanitation technology or across the whole system:
$$ LRV = log_{10}N_{0}log_{10}N = log_{10}\left(\frac{N_{0}}{N}\right) \quad (2) $$
The LRV is related to percent reduction, and one can be calculated from the other as shown in the following two equations:
$$ LRV = log_{10}\left(1\frac{E(\%)}{100}\right) = log_{10}\left(\frac{100}{100  E(\%)}\right) \quad (3) $$
$$ E(\%) = 100\times(110^{LRV}) \quad (4) $$
For instance, if the influent concentration is 1.00 × 10^{8} MPN/100 mL and the effluent concentration is 1.00 × 10^{5} MPN/100 mL, from Equation 1 it is seen that the reduction efficiency E is (1.00×10^{8}  1.00×10^{5})/(1.00×10^{8}) = 0.999, which, expressed as percent reduction efficiency E(%) is 0.999x100 = 99.9%. In order to express in terms of LRV, using Equation 2, one has: LRV = log_{10}(1.00×10^{8}) – log_{10}((1.00×10^{5}) = 8 – 5 = 3. Alternatively, the calculation can be done using the second part of Equation 2: LRV = log_{10}[(1.00×10^{8})/(1.00×10^{5})] = log_{10}(1.00×10^{3}) = 3.
Equations 3 and 4 can be used to convert E(%) into LRV and viceversa. Using Equation 3 or 4, it is seen that an efficiency of 90% corresponds to an LRV of 1 log_{10} unit; 99% ® 2 log_{10} units; 99.9% ® 3 log_{10} units; 99.99% ® 4 log_{10} units; 99.999 % ® 5 log_{10} units and so on. This relationship between percent reduction efficiency (E) and log_{10 }reduction value (LRV) is shown in Table 2.
In the Sanitation Technologies chapters and other locations of the Global Water Pathogen Project, pathogen reduction efficiencies are generally expressed as LRVs, using log_{10} units. This is because in some cases, pathogens in wastewater must be reduced by six or more orders of magnitude for the treated effluent or sludge to be safely reused, for example in agriculture (WHO, 2006). A reason for this is because it is cumbersome to refer to reduction as 99.9999%; it is much easier to say “6 log” reduction. Note that the term “log” here implies a base 10 logarithm (log_{10}), even if the subscript 10 does not necessarily appear after “log”. Pathogen reduction in sanitation technologies is almost never described in terms of natural logarithms, but if the natural logarithm is used in this context, it is denoted by the notation “LN”.
It is possible to have a LRV that is greater than the order of magnitude of the pathogen concentration in the influent. For instance, a pathogen that has an influent concentration of 1.00 × 10^{5} CFU/100 mL can be subjected to a treatment with a LRV of, say, 7. Rearranging Equation 2, it is seen that this will lead to log_{10}(10^{5})  7 = 57 = 2. The effluent concentration will then be 10(^{2}) = 0.01 CFU/100 mL. Of course, in this case, one must check whether this value is below the detection limits of the lab method used to enumerate the pathogen in question (considering the dilutions made to the sample prior to analysis and whether or not the sample was concentrated from a larger volume). If the value is above the detection limit, it can be reported as such. If it is below the detection limit, this could be mentioned after the calculation.
For sanitation treatment units placed in series, the overall efficiency of the combined treatment units is given by the multiplication of the remaining fractions of the constituent in each unit, which can be difficult to conceptualize. For instance, in a complete treatment system there may be three unit processes (i.e. sanitation technologies) placed in series, with the following reduction efficiencies in Unit A = 90%, Unit B = 99.9%, and Unit C = 99%. In this situation, the overall reduction efficiency will be:
$$ E_{overall}(\%) = 100\times\left(1\left[\left(1\frac{90}{100}\right)\times\left(1\frac{99.9}{100}\right)\times\left(1\frac{99}{100}\right)\right]\right) = 99.9999\%\space\text{(or } 6\space log_{10}\text{ unit reduction) } $$
However, if the pathogen reduction efficiencies in each unit are expressed as LRVs (Unit A = 1 log_{10}, Unit B = 3 log_{10}, Unit C = 2 log_{10}), then the relationship between the units in series is additive in terms of their individual LRV values, and much easier to calculate:
$$ LRV_{overall} = 1 + 3 + 2= 6\space log_{10}\text{ unit reduction (which is equivalent to 99.9999%) } $$
Individuals who estimate (model) how pathogens are reduced across a particular sanitation treatment technology are interested in whether pathogen concentrations are reduced over time and how to mathematically describe the rate of pathogen reduction. Kinetics deals with the rate of a reaction of a constituent in a reactor, that is, its transformation. Reactors can be operated in a batch or continuous flow regimens. For continuous flow regiments, when you have both the kinetics of pathogen inactivation and the transport of pathogens through the reactor, the model is called a process model. The following are two idealized types of reactors used in process models that have different hydraulic behavior and mixing conditions: completelymixed flow reactors (CMFRs) and plugflow reactors (PFRs). It is important to note that these two idealized reactors never occur in real life, where hydraulic behavior and mixing conditions lie somewhere between these two idealized extremes. Other models that represent more realistic hydraulics and mixing have been developed, and the use of these process models together with reaction kinetics is covered in many textbooks on chemical engineering and wastewater treatment, such as Levenspiel (1999), Arceivala (1981), von Sperling and Chernicharo (2005), von Sperling (2007), Kadlec and Wallace (2009), Metcalf and Eddy (2014), Mihelcic and Zimmerman (2014).
The reduction of pathogenic organisms frequently involves several mechanisms working simultaneously, and therefore it is usually difficult to model them individually. In almost all cases, pathogen reduction rates in sanitation technologies are sometimes expressed as pseudo firstorder reactions. Note there may be some pathogen inactivation mechanisms that follow secondorder kinetics, such as indirect sunlightmediated mechanisms for the inactivation of viruses (e.g. Kohn et al., 2016). However, for the purpose of this book, we will assume that pathogen reduction in sanitation system technologies generally follows pseudo firstorder kinetics. In this case, the rate of pathogen reduction is assumed to be proportional to the concentration at any given time, and is expressed as follows, where N is the pathogen concentration (i.e. MPN/100mL) at time t (i.e. minutes, hours, days) and k is the reduction or decay rate coefficient (inverse units of time; i.e. minutes1, hours1, days1, etc.):
$$ \frac{dN}{dt} = kN\quad{(5)} $$
The integration of Equation (5) yields the following, where No is the concentration at time t = 0:
$$ N = N_{0}e^{kt} \quad(6) $$
Note that the effluent concentration (N), and thus the reduction efficiency, depends on the unitless pair k × t. Therefore, to estimate the reduction efficiency of a sanitation treatment unit process that operates in batch mode, the reduction coefficient k and the retention time t are necessary inputs. For more information about typical pathogen reduction rates and coefficients, refer to the GWPP chapters on Persistence and Transport.
In batch experiments, the value of k may be estimated by regression analysis, having different pairs of values of t and N, that is, based on several samples taken at different times t and having different concentrations N_{t} (concentrations at time t). The value of k (and sometimes N_{o}) is the unknown in the regression analysis, that is, the parameter to be estimated. Simple linear regression, using the Method of Minimum Squares, can be done after linearization of Equation (6) by applying logtransformation on both sides of the equation, leading to ln(N_{t}) = ln(N_{o}) – k.t, with k being the slope of the line of best fit to the several experimental pairs of values (t, N_{t}). Alternatively, one can use Equation (6) directly, without linearization, and use nonlinear regression, obtaining the value of k based on an algorithm of minimization of the sum of the squared errors.
The more data points one has, the more reliable is the estimate of k. The least reliable estimate of k would be based on only two data points: one at the beginning of the experiment (t=0; N equal to the initial concentration N_{o} or N_{initial }and one at the end of the experiment, conducted for a duration over the total time t (t=t_{total}; N equal to the final concentration Nfinal). By inserting these values into Equation (6), one could calculate k by rearrangement of Equation (6), leading to k = ln(N_{initial}/N_{final})/t_{total.} This approach is not recommended because it does not allow for the confirmation that the decay rate is indeed indicative of firstorder (i.e., loglinear). Also, microbial decay rate curves frequently display shoulders and tails (Haas and Joffe, 1994), which would not be visible in a decay experiment with only two time points.
The first method, using a series of values collected over time and applying a regression analysis (linear or nonlinear), is more frequently applied by researchers when doing kinetic studies aiming at deriving the value of the reduction coefficient k.
The relative resistance of different pathogens to a particular set of conditions can be compared using the t_{90} time, which is the time required for 90% (1 log_{10}) reduction, or the t_{99} time, which is the time required for 99% (2 log_{10}) reduction. For firstorder and pseudofirst order reactions, the k value can be estimated from the t_{90} or t_{99 }time, for a batch reactor as shown below:
$$ k = \frac{ln(100/10)}{t_{90}}=\frac{2.3}{t_{90}}\quad\text{or}\quad{t_{90}}=\frac{2.3}{k}\quad(7) $$
$$ k = \frac{ln(100/1)}{t_{99}}=\frac{4.6}{t_{99}}\quad\text{or}\quad{t_{90}}=\frac{4.6}{k}\quad(8) $$
It is very important to emphasize that Equations (7) and (8) are only associated with batch reactors. Most estimates of the decay rate coefficient k for different pathogens reported in the literature come from bench or labscale studies that use batch system experiments to investigate the kinetics of pathogen inactivation, using the approach described above. However, it should be understood that a reliable determination of the “true” intrinsic decay rate coefficient k is not simple. As a result, reported values often vary considerably from study to study, even when highlycontrolled batch systems are used. To further complicate the usage of such kinetic coefficients, it should be remembered that fullscale sanitation technologies seldom operate in batch mode. Batch reactors are distinguished by the fact that, during the reaction time, they have no inlet or outlet flows. For instance, two examples of sanitation systems that can approach the behavior of batch reactors are a pit from a latrine that has been taken offline and is no longer in use or a sequencing batch reactor treating wastewater using the activated sludge process. Most sanitation technologies operate as continuous flow reactors, with liquid always entering and leaving the reactor. Furthermore, flow rates often have considerable variation both diurnally and seasonally. Therefore, in fullscale sanitation systems, unless the hydraulic behavior and mixing conditions are very wellcharacterized, decay rate coefficients obtained from bench or labscale studies should not be used, as they could produce very misleading results. This is an important warning regarding the widespread utilization of the expected “true intrinsic kinetic” k values derived from batch experiments: even if they may represent relatively well the decay rate of the constituent under study, the estimation of the effluent concentrations needs to take into account the hydraulic behavior and mixing conditions of the reactor, especially taking into account continuous flow reactors, as described in sections 2.2 and 2.3.
Most sanitation technologies utilize continuous flow reactors. Due to mixing in these reactors, not all pathogens spend the same amount of time in the reactor. Some flow through quickly, while others take longer to exit the reactor. The simplest estimate of the average time a pathogen or a water molecule spends in the reactor is calculated as the theoretical mean hydraulic retention time (HRT), using Equation (9), where V is the reactor volume (units of m^{3} or L, for example) and Q is the average flow entering and leaving the reactor (with units of volume/time, e.g., m^{3}/d or L/d):
$$ HRT = \frac{V}{Q}\quad(9) $$
Equation (9) shows that the dimension of HRT is time (typically days or hours). In order to estimate the effluent concentration of a continuous flow tank, it is necessary to know not only the decay rate coefficient k, but also the hydraulic behavior of the reactor. It should be remembered that the reactors can have different shapes (rectangular, square, irregular), different depths, the presence or absence of packing material, the presence or absence of plants and roots, different arrangements of inlet and outlet structures, different influences from wind, thermal stratification and circulation, dead zones, hydraulic short circuiting and several other factors that may substantially contribute to its departure from any idealized behavior.
Idealized flow regimens (Table 3) are often assumed when designing or modeling the behavior of reactors, however these represent idealized and extreme flow conditions. Actual flow conditions will be somewhere between these idealized and extreme conditions.
Equations 10 and 11 respectively present formulations for estimating the effluent concentration N in an idealized plugflow reactor and in an idealized completelymixed reactor, assuming steadystate conditions and firstorder kinetics. Both use the concept of the dimensionless pair k × t, or, in this case, k × HRT. This dimensionless pair imbeds not only the reaction kinetics, but also the hydraulic behavior of the reactor.
$$ \text{Idealized plugflow reactor:}\quad N= N_{0}e^{k.HRT}\quad(10) $$
$$ \text{Idealized completelymixed reactor:}\quad N= \frac{N_{0}}{1+k.HRT}\quad(11) $$
Note that the idealized plugflow reactor (Equation 10) behaves, theoretically, exactly as the idealized completelymixed batch reactor (Equation 6). Examining both of these equations shows that for a certain value of the product k × HRT, the ideal plugflow reactor leads to lower values of the effluent concentration N, compared with the completelymixed reactor.
There are other models that can be used in order to try to approach the actual hydraulic behavior of a tank, such as the dispersedflow model and the tanksinseries model. Both give better predictions of the actual behavior in a real reactor, but their application is beyond the scope of this chapter. Nonetheless, it is important to understand that when using the dispersedflow model, a reactor with zero dispersion yields the same results as the idealized plugflow reactor (Equation 10), and a reactor with infinite dispersion reproduces the idealized completelymixed model (Equation 11). Similarly, the tanksinseries model equals the completelymixed model when the number of reactors in series is one, and reproduces the plugflow model when the number of reactors in series is infinite. Of course, in existing reactors, the behavior is never idealized, and a certain degree of dispersion is likely to occur. In terms of a simplified hydraulic representation, each reactor may be represented by its dispersion number, which is a dimensionless variable that represents the relative importance of dispersion versus advection (which by definition is greater than zero and can theoretically approach infinity) for the dispersedflow model or by the equivalent number of tanks in series (usually 1 or greater) for the tanksinseries model.
For design purposes, one needs to select the flow conditions (batch or continuous flow reactor) and the hydraulic model for continuous flow reactors (plug flow, completelymixed or intermediate variants), and adopt values for the hydraulic retention time HRT and the reduction coefficient k. If it is considered that the hydraulic model represents well the fluid behavior and mixing conditions in the reactor, then the k value may be taken from literature, usually based on batch studies, as discussed in Section 2.1.
But in many cases, researchers opt to derive reduction coefficient (“k” values) based on real, existing, reactors, either in pilot or fullscale units. These “k” values that are calculated from pilot or fullscale continuous flow reactors should be labeled k’, to distinguish them from the true intrinsic coefficients, which we will label k. Considerable care needs to be exercised in the interpretation and use of such k’ values, here understood, not as true intrinsic coefficients, but rather as process coefficients, because they may incorporate in themselves, not only the influence of reaction, but also the unwanted influence of hydraulics and mixing.
In an existing batch reactor, the reduction coefficient k can be estimated based on measurements of the concentrations N at different time intervals t, as explained in Section 2.1.
In continuousflow reactors, the mean value of the reduction coefficient k is usually calculated based on:
For the two idealized flow regimens, rearrangement of Equations 10 and 11 leads to the following two equations for estimating the reduction coefficient (denoted k’ here to distinguish it from the true intrinsic decay rate coefficient as measured in batch system experiments):
$$ \text{Idealized plugflow reactor:}\quad k'= \frac{ln(N_{0}/N)}{HRT}\quad(12) $$
$$ \text{Idealized completelymixed reactor:}\quad k'= \frac{(N_{0}/N) 1}{HRT}\quad(13) $$
It is very important to understand again that the k reduction coefficient calculated this way for a fullscale sanitation system reactor is fundamentally different from the true kinetic coefficient (as determined in batch experiments in the laboratory) because it reflects not only the kinetics but also the particular hydraulic behavior of the reactor under study, and assigns it to a specified idealized regime (plug flow or completelymixed). These idealized conditions are never achieved in practice. Additionally, the actual HRT is likely to be different from the theoretical mean HRT (i.e. the volume divided by the flow rate; Equation 9), because of dead zones, short circuits, stratification, wind and other interferences (Verbyla et al., 2013).
For a given pathogen reduction efficiency, the estimation of k based on the hydraulic retention time (HRT) and on the influent concentration (N_{o}) and effluent concentration (N) on an existing continuousflow reactor leads to the two following divergent situations:
Example
The following example should help to clarify the point. An existing reactor has the following average values of performance indicators: (a) influent E. coli concentration: N_{0} = 1.00 x 10^{8} MPN/100 mL; (b) effluent E. coli concentration: N = 1.00 x 10^{6} MPN/100 mL; (c) theoretical hydraulic retention time (V/Q): HRT = 30 days.
From the data, it can be seen that the reduction efficiency is (N_{0}N)/N_{0} = (1.00 x 10^{8}  1.00 x 10^{6}) / (1.00 x 10^{8}) = 0.99 = 99%. Expressing in log_{10 }units removed gives log_{10}[(1.00 x 10^{8}) / (1.00 x 10^{6})] = log_{10}(100) = 2.00, or 2.00 log units reduced.
Use of Equations 12 and 13 will lead to the following estimated k reduction coefficients: plug flow: k = 0.15 d^{1 }(actually 0.1535 d^{1} to allow accurate calculations); completelymixed: k = 3.30 d^{1}. Therefore, for the same reactor, different k values are estimated in practice, depending on the hydraulic regime assumed (i.e., plug flow or completelymixed). The true kinetic coefficient (as obtained by batch experiments in the laboratory) will lie between the two values obtained for idealized plug flow and completelymixed models applied to actual continuousflow reactors.
In principle, there should be only one coefficient, representing the decay rate of the microorganism, according to its kinetics. However, the inadequacy of idealized models in representing the real hydraulic pattern in the reactor leads to the deviations that occur in practice when obtaining k values based only on influent and effluent concentrations in an existing reactor. The reason for the differences observed in the example above is that, since completelymixed reactors are the least efficient for firstorder reduction kinetics, the lower efficiency is compensated by a higher k value. Conversely, since plugflow reactors are the most efficient reactors, the k value is reduced to produce the same effluent quality. Depending on the dispersion characteristics of the reactor, the deviation can be very large, inducing considerable errors in the estimation.
An improvement in the estimation of k values from existing reactors is when the values are derived, not only from influent and effluent concentrations, but rather on a profile of concentrations measured along the reactor (for reactors that operate closer to plug flow conditions than completelymixed). For instance, sampling at different distances from the inlet (hence different travelling times) may give indications on the mixing conditions within the reactor and allow a better adoption of the selected hydraulic model. Furthermore, regression analysis (linear or nonlinear), using different pairs of travelling time t and concentration N) can be used to derive k (as explained in Section 2.1, applied to batch systems), for plugflow or dispersedflow models.
When reporting k values, it is essential that the researcher or practitioner specifies the conditions employed in the calculations:
As shown previously in Section 1, the overall log reduction in the treatment chain can be obtained by simply summing together the individual LRVs for each unit in series. This is why it is emphasized that, for this book, reporting the performance of each individual unit helps to clarify the actual behavior of each unit in the reduction of pathogenic organisms. However, for the same influent flow and concentration, increasing the volume of a single reactor (and hence its hydraulic retention time), adding extra treatment units in series, splitting a single reactor into several smaller ones, and improving flow conditions (reduction of dead zones and short circuits) can increase the efficiency of pathogen reduction in the overall system. However, the extent to which the efficiency improves depends on the flow regimen as shown in Figure 1.
Assuming that the flow rate Q does not change and the pathogen reduction coefficient k stays the same for each reactor throughout the treatment chain, for idealized plugflow reactors, doubling the total volume of the reactor will also double the expected pathogen reduction. However, under the same assumptions, increasing the number of units in series assuming idealized plugflow reactors without changing the overall volume with not affect the calculated pathogen reduction. For completelymixed reactors, this is not the case. Splitting a completelymixed reactor into smaller reactors in series with the same total volume (Figure 1b) substantially increases the calculated pathogen reduction, but not proportionally to the increase in volume, as is the case for plugflow reactors. Table 3 shows this effect in greater detail.
Adding a second completelymixed reactor after the first one (to double the overall volume) will double the pathogen LRV (again, assuming that k value remains the same in both reactors). The relative volume, expressed as the product of k × HRT (from Equations 10 and 11), is a way to demonstrate how much larger a treatment reactor needs to be in order to lead to a calculated higher percentage reduction efficiency or log reduction value. Using this approach, the relative volume required to achieve different reduction efficiencies in the idealized hydraulic regimens of completelymixed and plug flow can be calculated. For any given reduction efficiency, the idealized plugflow reactor requires a smaller volume than the idealized completelymixed reactor, as shown in Table 4.
For example, if the relative k × HRT value for 50% reduction efficiency is 1 for a completelymixed reactor (Table 4), it can be shown (using Equations 10 and 11) that to achieve the same percent or log_{10} reduction, the volume of a plug flow reactor would be 70% as big to achieve the same percent (or log_{10}) reduction. In other words, the idealized completelymixed reactor would need to be 1:0.7 = 1.4 times as large as the idealized plugflow reactor to achieve 50% reduction. As the percent or log_{10 }reduction goals get larger, this discrepancy between the idealized flow regimens increases. The volume of a completelymixed reactor would need to be 1087 times larger than a plugflow reactor to achieve a calculated 4log_{10} reduction. Therefore, as the log_{10} pathogen reduction requirements increase for wastewater treatment processes, having a good understanding about the extent of flow mixing becomes very important when trying to estimate pathogen decay rates. For this reason, estimates of pseudofirst order decay rates for pathogens from studies of fullscale systems can be quite confounded by the lack of a detailed understanding about hydraulic efficiency of the systems. For this reason, in the subsequent chapters, we focus on reporting the log_{10 }pathogen reductions (LRV) in different sanitation technologies rather than attempting to report apparent decay rate coefficients k (based on assumed flow regimens). For a detailed review of pathogen decay rates, refer to the chapters on Persistence (e.g. Pathogen Specific Persistence Modeling Data).
While reading the subsequent chapters related to the management of microbial risk from excreta and wastewater using specific sanitation technologies, here are a few important concepts to keep in mind:
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