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Determination the biochemical kinetics of natural and synthetic estrogens in moving bed Bioreactor
Zeynab Yavari1, Farzaneh Mohammadi2, Mohammad Mehdi Amin2
1 Department of Environmental Health Engineering, School of Health; Genetic and Environmental Adventures Research Center, Abarkouh Paramedical School, Shahid Sadoughi University of Medical Sciences, Yazd, Iran
2 Department of Environmental Health Engineering, School of Health; Environment Research Center, Research Institute for Primordial Prevention of Non-communicable Disease, Isfahan University of Medical Sciences, Isfahan, Iran
| Date of Submission | 02-Dec-2020 |
| Date of Acceptance | 02-Apr-2021 |
| Date of Web Publication | 23-Aug-2021 |
Correspondence Address:
Mohammad Mehdi Amin
Department of Environmental Health Engineering, School of Health, Isfahan University of Medical Sciences, Isfahan
Iran
 Source of Support: None, Conflict of Interest: None  | Check |
DOI: 10.4103/ijehe.ijehe_53_20
Aim: Estrogenic compounds as a group of endocrine disruptive compounds can interfere with endocrine system beings. In the present work, an attempt has been made, to characterize the kinetic coefficients of natural and synthetic estrogens, in a pilot-scale moving bed biofilm bioreactor (MBBR). Materials and Methods: The substrate removal rates were investigated at different organic loading rates, and hydraulic retention times. By applying some biokinetic models including first order, second order, Stover–Kincannon, and the Monod equation, the kinetic constants (m, Ks, k, Y, and Kd) were determined. Results: Estrogen-specific removal rate was between 0.22 and 1.45 μg. g VSS-1.d-1 for natural and synthetic hormones. The experimental data showed that the Stover–Kincannon model and second-order model were the fit models and have high correlation coefficients more than 99%. Conclusion: These findings indicated that theses mathematical models could be promising models for effectively predicting kinetic parameters for performance of MBBR reactors.
Keywords: Estrogens, kinetic constants, mathematical models
How to cite this article:
Yavari Z, Mohammadi F, Amin MM. Determination the biochemical kinetics of natural and synthetic estrogens in moving bed Bioreactor. Int J Env Health Eng 2021;10:4 |
How to cite this URL:
Yavari Z, Mohammadi F, Amin MM. Determination the biochemical kinetics of natural and synthetic estrogens in moving bed Bioreactor. Int J Env Health Eng [serial online] 2021 [cited 2023 Oct 4];10:4. Available from: https://www.ijehe.org/text.asp?2021/10/1/4/324280 |
| Introduction | |  |
Endocrine disruptive compounds (EDCs) are a wide range of natural and synthetic substances, which dispersed in the environment.[1] Steroid estrogens (SE) as a main class of EDCs have the most potent adverse health effects on wildlife especially in aquatics.[2] Some of the undesirable effects that are attributed to these pollutants include reduced fertility, bioaccumulative and intensely toxic on organisms, teratogenic, feminization, and carcinogenic, even in low concentrations.[3] Therefore, the Economic Partnership Agreement and European Union have listed SE as emerging contaminants. These priority pollutants included natural estrogens such as estrone (E1) and 17β-estradiol (E2) and synthetic steroid 17α-ethinyl estradiol (EE2).[4] Most of conventional wastewater treatment processes are designed to remove the organic matter and other pollutants with concentration in range of mg/L.[5] As regards the concentration of these emergency pollutants is very low ranging from a few ng/L to several μg/L, the removal efficiency of many of these micropollutants during wastewater treatment process is insufficient and imperfect.[6],[7] The presence of these contaminants in to receiving water is the result of the effluent discharge flow from sewage treatment plants and due to estrogenic activity considered as a risk for aquatic ecosystem.[8]
During conventional WWTPs, the removal efficiency of estrogenic compounds is not sufficient and perfect. Nevertheless, numerous study illustrate a wide range from 76% to > 90% for EE2, 19% to 98% for E1, and 62% to 98% for E2.[9] Optimizing the performance and stable operation are design criterion for the biological wastewater treatment. Recently, the proper design of bioreactors affected by empirical and logic parameters based on biological kinetic equations. Biokinetic parameters make useful information about the rate of microbial growth and consumption of substrate.[10] These coefficients are calculated to understanding well the process control and predict the implementation of a biological process. For getting the high efficiency of bioreactor, it necessary to considered the kinetic coefficients instead of empirical methods. However, uncomplicated models with few variables are more suitable for monitoring and field applications of biological reactors.[11] Specific growth rate (μ), maximum rate of substrate utilization per unit mass of microorganisms (k), half-velocity constant, or substrate concentration at one-half the maximum specific growth rate (Ks), maximum cell yield (Y), and endogenous decay coefficient (kd), are major biological kinetic coefficients that used for design the activated sludge processes.[10] Numerous studies have been carried out to evaluate the kinetic constants in the different wastewater treatment processes. These values are compared in [Table 4]. Borghei determined biokinetic coefficients for a biomass reactor for treating a synthetic wastewater including sugar manufacturing. He reported the Stover–Kincannon model and Grau model showed the most coordination.[11] Fikret Kargi evaluated the kinetic constants of synthetic wastewater containing 2, 4-dichlorophenol by rotating perforated tubes biofilm reactor.[12] The biological kinetics for activated sludge process in municipal wastewater was determined by Mardani et al.,[10] Wong et al., evaluated the biokinetic coefficients for palm oil mill effluent on anaerobic stabilization pond treatment. These findings indicated that Y, kd, Ks and μmax coefficients were of 0.990 g VSS/g chemical oxygen demand (COD), 0.024 day−1, 0.524 day−1, 203.433 g COD l−1, respectively.[13] Among the biological process for wastewater treatment, the most effective and benefits are attached growths. The moving bed biofilm reactor (MBBR) is an attached growth process that was constructed based on activated sludge process. Advantages of MBBRs include the reduction in space as compared to conventional activated sludge, facilitate, and enhance the growth of slow-growing microorganisms due to high SRT, redox conditions within biofilm that enhance the removal of micropollutants.[14] | Table 4: Comparison of kinetic constants in the different models cited in the literature with results of the present study
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There is also not enough information in the literature to analytically determine the biokinetic coefficient of natural and synthetic hormones in MBBR. Four common mathematical models such as first-order, second-order, Monod, Stover-Kincannon are used for evaluate the biodegradability of SE in MBBR. There has also been little effort dedicated toward the development of a better fundamental and conceptual illustrating of kinetic parameters of natural and synthetic hormones in biological wastewater treatment. The main objective of this article is to assessment the elimination efficiency of E1, E2, and EE2 in MBBR and development a kinetic model to represent the performance of this process. The target analytes were extracted by dispersive liquid liquid microextraction, and identified by gas chromatography followed with mass spectrometry (GC-MS).
| Materials and Methods | | |
Experimental set-up
It can be seen a schematic of the moving bed bioreactor (MBBR) [Figure 1]. The Polypropylene carriers had specific surface 400 m2/m3 and density 0.97 g/cm3. | Figure 1: Schematic diagram of the lab scale moving bed biofilm reactor system
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Synthetic wastewater composition is illustrated in [Table 3]. Wastewater spiked with target analytes at different organic loading rate was introduced to the reactor through pump (Etatron-Italy). COD spiked with hormones was considered as influent substrates for biokinetic study [Table 3]. By modifying the flow rate of the influent, HRT was controlled. The parameters required for the biokinetic values calculation summarized in Nomenclature.
Analytical methods
Common operating parameters including COD, sCOD, rbCOD, MLSS, TSS, and VSS were measured according to the standard methods.[15] The attached-growth biofilm was determined by procedure was described by Amin et al.[16]
For extraction, the target analytes from wastewater samples, 5 ml of effluent spiked with 10 μL of n-Octyl Phenol as internal standard, 100 μL of chloroform (extractive solvent) and 500 μL of methanol (dispersive solvent) injected rapidly into tube. Then, cloudy solution centrifuged for 5 min at 5000 rpm. The lower phase extracted and transferred into a 2 mL vial to dryness under a gentle flow of nitrogen.[17] The dry residue was derivatized with 10 μL of BSTFA containing 1% of TMCS (as derivative agent) and 20 μL pyridine and heated at 70°C for 30 min in a water bath.[18]
GC–MS analysis was carried out using a gas chromatograph (7890A Agilent Technologies, USA) interfaced with a mass spectrometry (5975C series). For qualitative and quantitative analysis, The MS was operated in SIM scan mode from m/z, 50–600.[19] The ratio of m to z (m/z) was 342, 416 and 425 correspond to E1, E2 and EE2, respectively.[20] [Figure 2] shows the chromatogram of 17-α ethynil estradiol, estrone and 17-β estradiol. All experiments were performed in triplicates. | Figure 2: Removal efficiency of chemical oxygen demand, E1, E2, and EE2 at different HRTs
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Mathematical model development
Monod equation
The Monod equation is a mathematical model, which has been widely used for the microbial growth and the kinetics, to explain the biodegradation of pollutants. This model is used for obtaining the empirical coefficients ks and K.
By considering the steady state conditions, the changing rate of substrate concentration can be neglected (ds/dt = 0) and Equations (1) and (2) can be rewritten as Equation (3):
Ks and k half which are saturation constant and the maximum rate of substrate consumption, respectively, obtained by plotting the 1/S versus Xatt/(Q (S0-S)). In equation 3, (A. XA) is known as Xatt, the slope of this graph is K/ks, and the intercept is 1/ks. The Y and Kd coefficients were derived by the mass balance equation and the monod growth kinetic for biomass, as rewritten in Equations (4) and 5):
As above-mentioned, under steady state conditions, the term of dx/dt is negligible (dx/dt = 0), and by integrating of Equations (4) and (5) rearranged Equation (6) as follows:
By the linear regression of (S0-S)/X versus Xatt/QX, (Y) and (Kd) can be determined subsequently. The maximum specific growth rate coefficient (μm) is attained by Equation (7) as follow:[21]
First order kinetic
In complete mix reactor, the rate of changes in substrate concentration complies with first-order kinetic, which expresses as follow:
If the steady state conditions predominated in the complete mixed reactor, the left section of equation 8 removed and the Equation (8) is simplified to Equation (9):
The k1 value can be achieved from the slope of line which plotted the ((S0-S)/HRT) versus S.
Stover–Kincannon model
In this model, the substrate utilization rate for biofilm reactors is a function of organic loading rate Equation (10), and Equation (11) can be obtained from the linearization of Equation 10 as follows:
Second-order kinetics (Grau model)
The general equation of second-order kinetic model which presented by Optaken (Optaken, 1982) and Grau et al.(Grau et al., 1975) is demonstrated in Equation (12).
By integrating and linearizing Equations (12) and (13) is demonstrated as:
If the first term of the right part of Equation 13, is considered constant, and (S0-S)/S0 accepts as the substrate removal efficiency and represented with E, the final equation can be summarized as follows:
| Results | | |
Moving bed biofilm reactor operation
The biodegradability of steroid hormones and the biokinetic coefficient evaluation carried out in MBBR. [Table 2] summarizes the steady state operation of MBBR at various HRT of 4, 8, 12, 16 h. The removal efficiency of COD and sCOD corresponding to HRT is illustrated in [Figure 2]. By decreasing the COD loading rate (from 3 to 0.75 kg/m3.d), COD removal was increased. In addition, COD removal was increased from 86% to 97% by decreasing the loading of target analytes. According to these results, COD and sCOD removal efficiency was increased by increasing the HRT. In addition, increasing the loading of E1, E2 and EE2 cause to reduce the removal of COD. These results indicated the high removal of COD was acceded in all of experiment (88%–97%) and the sCOD concentration in effluent was lower than 20 mg/L. Minimum removal rates of E1, E2, and EE2 (81, 98.5 and 76%, respectively) was achieved at HRT 4 h. By gradual increasing the HRT, removal efficiency of E1, E2, and EE2 augmented and obtained 98, 99.9, and 95%, respectively, at high HRT (16 h). In general, during the operation of MBBR, the elimination rate of natural and synthetic estrogens was more than 90%. As can be seen, the removal efficiency of steroid hormones was not much significance difference at the higher HRT of 12 and 16 h. SRT and HRT are two critical parameters for operating of MBBR. At high SRT, the microbial consortium for degradation of steroid hormones enhanced the biodiversity of microbial for degradation of rebellious pollutants such as EE2.[22]
First order kinetic
As shown in [Figure 3], the coefficient of first-order kinetic for substrate removal was obtained by plotting between (S0-S)/HRT versus S. According to Eq 9, from the slope of this line k1 coefficient was achieved. This value for different concentration (5, 10, and 50 μg/L) was 16.76, 17.87, and 19.67 per day, respectively. The performance of MBBR can't be predicted by this model, because the correlation coefficient was very low for all concentrations (<0.8). | Figure 3: First order kinetic model for wastewater containing E1, E2, and EE2
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Second-order kinetic (Grau model)
[Figure 4] pinpoints the second order model (Grau model) for elimination of substrate. The kinetic coefficients of a, b and k (2) s at Equation (13) was achieved by plotting the (S0.HRT)/(S0-S) versus HRT. At concentration of E1, E2, and EE2 equal to 5 μg/l, the values of a, b, and k (2) s were found to be 0.052, 1.057, and 0.472, respectively. The correlation coefficient was 0.996. For concentration 10 μg/l of target analytes, these coefficients were obtained 0.0472, 1.0311, and 0.572, respectively, with high correlation coefficient (0.997). Finally, at concentration 50 μg/l of steroid hormones, the value of kinetic coefficient were 0.053, 0.9721 and 0.546 d−1, respectively. In addition, (R2) was 0.999. It seems the Grau model have a good suitability for predicting the MBBR performance. | Figure 4: Second-order model (Grau model) for wastewater containing E1, E2, and EE2
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Stover– kincannon
[Figure 5] indicates the linear regression of Stover-Kincannon modified model which achieved by plotting the  against  . The value of Umax, which was computed from the equation line in graph 4 at influent concentrations (5, 10, and 50 μg/l) of hormones, was 5.66, 10.17, and 11.6 g/l.d, respectively. This finding illustrated, by increasing the concentration of these micropullatants, the maximum substrate elimination was obtained. The KB constant values were 5.9,105 and 11.5 g/l.d. Moreover, the high value of correlation coefficient of 0.97, 0.991, and 0.997 declared the Conformity of this model with high precision for the MBBR performance. | Figure 5: Stover–Kincannon model for wastewater containing E1, E2, and EE2
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Monod equation
Monod's equation explain the dependence of microbial degradation rate on the of biomass concentration. A mass balance for microbial mass and Monod equation can be used for calculating the kinetic coefficients of K, ks, Y, Kd and μmax in biofilm systems. The Ks and K value for synthetic wastewater (COD = 500 mg/l) containing E1, E2, and EE2 = 5 μg/l was calculated as 49.07 and 0.326 mg/L, respectively. These coefficients for concentrations of 10 and 50 μg/l were 12.32, 0.218, and 7.25, 0.2 as mg/L, respectively. High correlation coefficient (more than 95%) for these concentrations as depicted in [Figure 6], illustrates a good model for calculating kinetic coefficients in biological process. [Figure 7] shows the graph plotted between reciprocal of Xatt/Q. X versus the (S0-S)/X for computing the Y, Kd and μmax. The Y, Kd coefficients for 5 μg/L were 0.515 and 0.018 d−1. These values for 10 and 50 μg/L were 0.7, 0.17 and 0.64, 0.01 d−1, respectively. The (Ks) value for SEs in 5, 10, and 50 μg/l was 39.07, 12.3, and 7.2 mg/L, respectively. In addition, (k) value was 0.27, 0.22, and 0.21 d−1 for estrogen compounds as substrate, respectively [Figure 6]. | Figure 6: Linear regression for determination of (Ks) and (k) for wastewater containing E1, E2, and EE2
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 | Figure 7: Linear regression for determination of (y) and (Kd) for wastewater containing E1, E2, and EE2
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| Discussion | | |
Evaluation of kinetic models
[Table 4] summarizes the constants coefficient evaluated on COD basis determined from the kinetic models in this study and compared with other studies. This result has highlighted, for prediction the performance of MBBR, the Stover–Kincannon and Grau second-order kinetics were more conformity. The Monod and Stover–Kincannon (R2 > 0.9), illustrates that the modified Stover–Kincannon model were more appropriate model for describing the kinetics of the MBBR treating estrogens wastewater. The constant coefficients of Stover–Kincannon model (KB and Umax) were lower than those reported by others [Table 4].[23] Hosseini and Borghei were reported similar observations for synthetic wastewater containing beet sugar molasses.[11] Nonetheless, Ahmadi et al. reported the higher values of Umax and KB for DEP and DAP.[24]
According to the second-order model (Grau model) results, the k (2) s coefficient measured in this research was in the range of k (2) s values that acquired in other researches. According to concentration of influent substrate and the biomass in the reactor, the k (2) s value will be increased by the removal rate of substrate. In conclusion, the k (2) s coefficient gradually decreased by increasing the target analytes concentrations, show conformity to recorded results from the Stover–Kincannon model. Kinetic constants Ks, k, Y, kd, μmax were obtained by using the modified Monod's equation at different concentrations. It can be seen; the value of (kd) Had a declining rate by increasing the concentrations of steroids and based on the COD were 0.06 and 0.045, respectively. As illustrated in [Table 2] the effluent substrate concentration showed the direct effect on kd and Ks values while had inverse effect on μmax value. In the study of Hamoda and Al-Attar, it was concluded that the values of kd for activated sludge and fresh waters were 0.3 and 0.16, respectively. Related findings were described the Ks values affected by the nature of the substrate.[10] The maximum specific growth rate is agree with the studies, which investigated by Mardani et al.,[10] Al-Malack,[25] YU,[26] Samuel Suman Raj.[27]In general, it is clear from [Table 3] that the change of SE concentrations coefficients did not affect the coefficients. It can be concluded that the presence of estrogenic compounds did not have inhibitory effect on biological treatment. The potential degradation of natural and synthetic estrogens by various isolated bacterial strains from activated sludge confirmed by many publications. In addition, numerous study characterized the estrogens can be used as only source of energy and carbon which metabolized by bacterial strains in wastewater treatment plant. On the other hand, the strain could be cultivated on estrogens. However, this variability might be originated from the nature of the system itself to select a process and obtained kinetic coefficient from different species.[25] The same occurrence happened at other concentrations also.
| Conclusion | | |
The result of this study demonstrated that the natural and synthetic SEs could be treated effectively through MBBR. With respect to the bio-kinetic coefficients of the MBBR process, the findings indicated the coefficients, except that of ks, were accommodated with the conventional activated sludge processes recorded in the literature. The biokinetic coefficients that achieved from the experiments will be useful for prediction the overall efficiency in treatment plants. It was also postulated that overall biodegradation of estrogenic compounds was influenced by increasing of HRT. It is also concluded that MBBR could be an excellent alternative as attached growth process for treating estrogen wastewaters. Results from the whole experiments, indicated that the biodegradability of hormones in order E2, E1 and EE2. Accordingly, EE2 and E2 are recalcitrant and easily estrogenic hormones for biodegradation, respectively.[33]
Financial support and sponsorship
This work was supported by Isfahan University of Medical Sciences, Isfahan, Iran, as research project [grant number: 394774].
Conflicts of interest
There are no conflicts of interest.
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[Figure 1], [Figure 2], [Figure 3], [Figure 4], [Figure 5], [Figure 6], [Figure 7], [Figure 1], [Figure 2], [Figure 3], [Figure 4], [Figure 5], [Figure 6], [Figure 7]
[Table 1], [Table 2], [Table 3], [Table 4], [Table 1], [Table 2], [Table 3], [Table 4]
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