Electrochemical Mineralization of Ibuprofen on BDD Electrodes in an Electrochemical Flow Reactor: Numerical Optimization Approach

: Statistical analysis was applied to optimize the electrochemical mineralization of ibuprofen with two boron-doped diamond (BDD) electrodes in a continuous electrochemical ﬂow reactor under recirculation batch mode. A central composite rotatable (CCR) experimental design was used to analyze the e ﬀ ect of initial pH (2.95–13.04), current intensity (2.66–4.34 A), and volumetric ﬂow rate (0.16–1.84 L / min) and further optimized by response surface methodology (RSM) to obtain the maximum mineralization e ﬃ ciency and the minimum speciﬁc energy consumption. A 91.6% mineralization e ﬃ ciency ( E M ) of ibuprofen with a speciﬁc energy consumption ( E C ) of 4.36 KW h / g TOC within 7 h of treatment was achieved using the optimized operating parameters (pH 0 = 12.29, I = 3.26 A, and Q of 1 L / min). Experimental results of RSM were ﬁtted via a third-degree polynomial regression equation having the performance index determination coe ﬃ cients (R 2 ) of 0.8658 and 0.8468 for the E M and E C , respectively. The reduced root-mean-square error (RMSE) was 0.1038 and 0.1918 for E M and E C , respectively. This indicates an e ﬃ cient predictive performance to optimize the operating parameters of the electrochemical ﬂow reactor with desirability of 0.9999993. Besides, it was concluded that the optimized conditions allow to achieve a high percentage of ibuprofen mineralization (91.6%) and a cost of 0.002 USD $ / L. Therefore, the assessed process is e ﬃ cient for wastewater remediation.”


Introduction
Over the last decade, water contamination has increased due to industrial activities. In this context, the pharmaceutical industry is of great concern since elements of its waste have been detected in the aquatic environment [1]. These contaminants are classified as emerging contaminants [2] and in concentrations up to 10 mg/L might have negative effects on human health [3]. Also, emerging contaminants can cause chronic toxicity and interference in the regulators of reproduction of vertebrates and invertebrates [4]. The most used anti-inflammatory drugs in Mexico include diclofenac, paracetamol, naproxen, and ibuprofen (IBU). These can be purchased without medical prescription, so their consumption is not regulated. All these compounds are considered emerging contaminants and IBU is one of the most worldwide consumed drugs [5]. IBU is an anti-inflammatory drug and it is prescribed for fever and to deal with inflammatory diseases like rheumatoid arthritis and osteoarthritis [3]. Different technologies have been evaluated to prevent the accumulation and destruction of IBU in the aquatic environment, such as physicochemical [6], biological [7], chemical [8,9], and advanced oxidation processes (AOPs) [10]. Table 1 presents the performance of other methods applied for the oxidation of IBU.  [10] IBU mineralization has also been assessed by electro-oxidation. Such a process consists mainly of the hydroxyl radicals production at the electrode surface and therefore the efficiency of the process has been reported to depend on electrode type, applied electrical current and the effect of pH is controversial. Electro-oxidation is an electrochemical advanced oxidation process (EAOP) and it has been considered as a green technology for wastewater treatment since the main oxidant species, hydroxyl radicals, are produced without the further addition of dangerous chemicals [11]. To produce hydroxyl radicals on an electrode surface and perform an effective degradation and mineralization of organic pollutants, an adequate anode must be employed under appropriate reaction environments. In literature, the anodes of Pt/BDD [3], Ti/Pt/PbO 2 and Ti/BDD [12], multi-walled carbon nanotube [13], Pt [14], and PtRu [4] are anode materials that have been used to carry out the degradation of IBU. In previous studies on electrochemical degradation of IBU, the boron-doped diamond (BDD) anode has demonstrated to be a good alternative for the total organic carbon (TOC) removal from an IBU synthetic solution since 92% and 96% removal was obtained with the current density of 30 mA/cm 2 and 500 mA/cm 2 , respectively, within 8 h of electrolysis on 200 mL of synthetic IBU solution [3,12]. Unfortunately, these works concluded that the high production cost of BDD electrodes makes the use of BDD anode not feasible for large-scale applications. Nevertheless, there are in the literature some important applications of BDD anode at a large-scale, which include the electro-oxidation of low-salinity reverse osmosis membrane concentrate [15,16] and the removal of organic contaminants (such as IBU, atrazine, diclofenac, among others) from a secondary effluent of real wastewater in a divided electrochemical filter-press reactor with BDD anode (40.8 cm 2 of an electroactive area), where the reactor was separated by a cation exchange membrane Ultrex CMI-7000. The main result of such investigation was that high removal of IBU achieved within 24 h of electrolysis time [17]. Although there are many studies about the degradation of IBU, only a few focuses on optimization. Such studies include the removal of IBU by absorption using mesoporous carbon aerogel [18], photooxidation of IBU using thin films of PAA/PAH/TiO 2 [19], nano-photocatalytic degradation of IBU by using Ultraviolet C/ZnO [20], IBU degradation by a three-dimensional electro-Fenton process [21], and sonoelectrochemical oxidation of IBU [22]. Thus, based on the literature survey, it can be concluded that the electrochemical degradation of IBU is feasible but needs to be optimized to reduce the overall cost of the process.
The main objective of this work was to conduct the statistical optimization of operating variables such as initial pH (pH 0 ), current intensity (I), and liquid volumetric flow rate (Q), during the IBU electrochemical mineralization when using BDD electrodes as cathode and anode. To accomplish this, the response surface methodology (RSM) based on a central composite rotatable (CCR) experimental design was applied.

Synthetic Solution of Ibuprofen
All experiments were conducted with a solution containing IBU (40 mg/L, 35 mg of TOC/L) and Na 2 SO 4 (0.1 M). This synthetic solution was prepared by adding the reagents into a reservoir with distilled water to dissolve the IBU. The IBU solution was homogenized by recirculating it for 2 h through the reaction system without applying any current intensity. It is worth mentioning that all solutions were prepared right before performing each experiment. The pH of the IBU solution was adjusted with NaOH (1 M) or H 2 SO 4 (1 M). Both compounds were supplied in 97% purity by Meyer IBU (99% purity) was supplied by Sigma-Aldrich and Na 2 SO 4 (99% purity) was supplied by Fluka. The chemical structure and physicochemical properties of IBU are summarized in Table 2.

Synthetic Solution of Ibuprofen
All experiments were conducted with a solution containing IBU (40 mg/L, 35 mg of TOC/L) and Na2SO4 (0.1 M). This synthetic solution was prepared by adding the reagents into a reservoir with distilled water to dissolve the IBU. The IBU solution was homogenized by recirculating it for 2 h through the reaction system without applying any current intensity. It is worth mentioning that all solutions were prepared right before performing each experiment. The pH of the IBU solution was adjusted with NaOH (1 M) or H2SO4 (1 M). Both compounds were supplied in 97% purity by Meyer IBU (99% purity) was supplied by Sigma-Aldrich and Na2SO4 (99% purity) was supplied by Fluka. The chemical structure and physicochemical properties of IBU are summarized in Table 2.  Figure 1 shows the reaction system used to carry out the electrochemical mineralization of IBU. The experimental set-up is constituted by an electrochemical flow reactor (EFR) with a volume of 3.52 × 10 −5 m 3 , two BDD electrodes (a thickness of 5 μm supported on Nb) that are separated 1.1 cm from each other, a glass rotameter to measure the volumetric liquid flow rate, a pump to recirculate the synthetic solution and a reservoir to supply the IBU synthetic solution. The circulation  Figure 1 shows the reaction system used to carry out the electrochemical mineralization of IBU.

Synthetic Solution of Ibuprofen
All experiments were conducted with a solution containing IBU (40 mg/L, 35 mg of TOC/L) and Na2SO4 (0.1 M). This synthetic solution was prepared by adding the reagents into a reservoir with distilled water to dissolve the IBU. The IBU solution was homogenized by recirculating it for 2 h through the reaction system without applying any current intensity. It is worth mentioning that all solutions were prepared right before performing each experiment. The pH of the IBU solution was adjusted with NaOH (1 M) or H2SO4 (1 M). Both compounds were supplied in 97% purity by Meyer IBU (99% purity) was supplied by Sigma-Aldrich and Na2SO4 (99% purity) was supplied by Fluka. The chemical structure and physicochemical properties of IBU are summarized in Table 2.   The experimental set-up is constituted by an electrochemical flow reactor (EFR) with a volume of 3.52 × 10 −5 m 3 , two BDD electrodes (a thickness of 5 μm supported on Nb) that are separated 1.1 cm from each other, a glass rotameter to measure the volumetric liquid flow rate, a pump to recirculate the synthetic solution and a reservoir to supply the IBU synthetic solution. The circulation The experimental set-up is constituted by an electrochemical flow reactor (EFR) with a volume of 3.52 × 10 −5 m 3 , two BDD electrodes (a thickness of 5 µm supported on Nb) that are separated 1.1 cm from each other, a glass rotameter to measure the volumetric liquid flow rate, a pump to recirculate the synthetic solution and a reservoir to supply the IBU synthetic solution. The circulation pipe has an inner diameter of 1.27 cm. Energy was supplied by a single output DC power supply. All experiments were carried out at 25 • C and atmospheric pressure. A detailed description of the EFR has been previously reported [25].

Electrochemical Mineralization of IBU
The electrochemical mineralization of IBU was performed in the experimental set up depicted in Figure 1. In a typical experiment, 2.5 L of an IBU solution were loaded in a continuous stirred tank (see Figure 1). This solution was prepared as described in Section 2.1. The solution was then recirculated through the system by means of a pump. The liquid flowrate was regulated with a rotameter. In this way the IBU solution was continuously fed through the electrochemical flow reactor (EFR). The exit stream of the EFR was taken to the continuous stirred tank and recirculated again. The studied variables were I, Q, and pH 0 , according to Table 3. The mineralization of IBU was verified by using TOC analysis (6001 TOC analyzer, Shimadzu, Instrumentation and Service in Analytica, S.A. de C.V., Calz, Mexico). For this purpose, samples at the beginning and after 7 h of electrolysis time were taken for each operating condition. All experiments were performed by duplicate. The reported mineralization efficiency and specific energy consumption is the average of the obtained results. The total number of experiments for the optimization process is presented in Table 4. Table 3. Values and levels of operating parameters.  Table 4. CCR experimental design for electrochemical mineralization of IBU. In addition, the electrochemical mineralization of IBU was conducted at the optimal conditions in order to establish the TOC removal kinetics. For this experiment, 10 mL aliquots were taken every 25 min during 7 h.

Optimization Process
Typically, an optimization process is conducted by changing one variable while keeping the others constant, until all variables have been investigated. However, this procedure implies a large number of experiments, and the combined effect of two variables or more might be missed [26].
The response surface methodology (RSM) is the preferred numerical tool to conduct a statistical analysis of the influence of process variables and to determine the optimum operating environments with a relatively small quantity of experiments. To accomplish this, the central composite rotatable (CCR) experimental design is a standard design of experiments (DOE) to conduct experimental planning and provide a sufficient amount of data for testing a lack of fit [27]. Central composite (CC) experimental design is based in two-level (−1, +1) factorial designs (full 2 k , k is the number of factors), augmented with 2k centered points (0) and 2k axial points with two-levels (−α, +α). A design is called rotatable when the variance of the predicted response at any point depends only on the distance of the point formed from the centered points of design and a CCR experimental design has five-levels for each factor. The rotatable design provides uniformity in the prediction error and it is achieved by proper choice of α (α = 2 k/4 ) [28].
For this study, the values and levels of each operational parameter are summarized in Table 3. The pH is an important factor in wastewater treatment [29], and this is not the exemption. In this work, the studied pH range was established according to the hydrophobic and hydrophilic character of IBU. At pH lower than 4.9, IBU remains as a molecule, its solubility decreases and tends to precipitate [14]. At pH higher than 4.9, IBU hydrophilic character increases. Regarding liquid flow rate (Q), in a previous study [25] with the same reactor albeit with another organic molecule, the optimal Q was found to be in the interval of 0.5-1.5 L/min. Thus, it was decided to use a similar interval here. The values of the electrical current (I) were selected within the typical range used in environmental applications, especially in electro-oxidation processes [30].
The operating parameters tested can be coded by Equation (1): Table 4 presents the authentic and coded values for the three operating variables chosen for the experimental design. The results obtained in terms of two measured response factors (dependent variables), namely mineralization efficiency (E M , response factor η 1 ), and specific energy consumption in kW h/(g TOC) (E C , response factor η 2 ) are presented in Table 4.
In RSM the selected operational parameters must be analyzed as observed responses employing a third-degree polynomial function (Equation (2)), where β values are the regression coefficients and ε is the error. The β parameters of the polynomial equation were computed by using step-wise regression. This type of regression is a combination of forward and backward regressions, starting with two forward steps. An analysis of variance (ANOVA) was applied to the experimental data for the determination of the model. The β values were computed by regression analysis of data. The significant effect of β values can be tested by means of a statistical significance test (p ≤ 0.05). Also, the coefficient of determination, R 2 , indicates the adjustment degree of the polynomial model. In this work, the Design-Expert ® V. 10. software (Multion Consulting, S.A. de C.V, Calz, Mexico) was used to design the experiments, to perform, and to analyze the multiple regression, and to generate graphics of experimental data and results. Finally, the model accuracy for two responses was evaluated using the reduced root-mean-square error (RMSE). Performance index RMSE is represented by Equation (3) [31]: where η l, Pred is the response obtained by the model, η l, Exp is the response obtained experimentally, and n is the number of experiments.

Analytic Procedure
The mineralization efficiency of IBU was calculated employing Equation (4): where TOC 0 and TOC t refer to the target total organic carbon concentrations before and after reaction time, respectively. The specific energy consumption (E C , kW h/g TOC) was calculated according to Equation (5) [32]: where ∆(TOC) Exp is the removal of ∆TOC values at t (h), I is the current intensity (A), E cell is the average cell potential (V), and V s is the volume of the treated synthetic wastewater (L). Finally, the real cost of the electrolysis process can be calculated by Equation (6) [33]: where Cost is the operation cost of the continuous electrochemical flow reactor and $MXP/kW h is the cost per kW h. The average cost per kW h in Mexico to industries is $2.806 MXP (CFE, Mexican Federal Electricity Commission) in November 2020.

Assessment of Experimental Results with Design-Expert ®
To explore the effects of the variables pH 0 (X 1 ), I (X 2 ), and Q (X 3 ) on mineralization efficiency (η 1 ) and energy consumption (η 2 ), the dependency of these variables was analyzed and modeled. From this analysis, a third-order model was employed to obtain a very good accuracy on both, modeling and optimization. In this particular case, a second-order model does not meet the criteria for a good predictive model. These criteria are the p-value of the model ≤ 0.05, the p-value of the lack of fit > 0.1, and the adjusted R 2 ≥ 0.8 [34]. Third-order models that describe the variation of the selected responses are given by Equations (7) and (8): Inters o f coded f actors Inters o f uncoded f actors Inters o f coded f actors Inters o f uncoded f actors From the ANOVA of results (Table 5), it can be observed that the two found third-order models were significant because they have low probability values [35] (0.0071 and 0.0044 for E M and E C , respectively). To indicate an adequate signal for the model, adequate precision ratios greater than 4 must be achieved [36]. For these tested models (E M and E C ), the adequate precision ratio of the models was 12.33 and 18.77, respectively. Additionally, in this study, the lack-of-fit F-test was statistically not significant because the values of Prob > F (0.5370 and 0.5334 for E M and E C , respectively) were greater than 0.005, which implies a significant model correlation between variables (X 1 , X 2 , and X 3 ) and responses (η 1 and η 2 ). Moreover, the R 2 values were 0.8658 and 0.8468 for η 1 and η 2 , respectively, which indicates a good model fitting [37].
Furthermore, the performance index RMSE for both responses (η 1 , and η 2 ) was computed by using Equation (3), where the values were 0.1038 and 0.1918 for mineralization efficiency and energy consumption, respectively. Small values of RMSE indicate that the developed models (Equations (7) and (8)) are in concordance with experimental results.
The parity plots shown in Figure 2 are evidence of the model suitability. Figure 2 shows there is a good correlation between experimental data and predicted values for both responses (E M (%) and E C (KW h/g TOC). Also, the coefficients of variation (CV) values are lower (12.82% and 18.77% for E M and E C , respectively). This indicates that the applied third-degree models are precise and reliable [38]. Furthermore, the performance index RMSE for both responses (1, and 2) was computed by using Equation (3), where the values were 0.1038 and 0.1918 for mineralization efficiency and energy consumption, respectively. Small values of RMSE indicate that the developed models (Equations (7) and (8)) are in concordance with experimental results. The parity plots shown in Figure 2 are evidence of the model suitability. Figure 2 shows there is a good correlation between experimental data and predicted values for both responses (EM (%) and EC (KW h/g TOC). Also, the coefficients of variation (CV) values are lower (12.82% and 18.77% for EM and EC, respectively). This indicates that the applied third-degree models are precise and reliable [38]. The coefficients of the tested cubic models (Equations (7) and (8)) indicate the relative effect of the independent factors (X1, X2, and X3) on responses (EM and EC). On the basis of the coefficients in Equation (7), it can be noted that the mineralization efficiency (EM) decreases with pH0 (X1), I (X2), and Q (X3). A positive effect of the interaction between the variables of pH0 and I (X1X2), and pH0 and Q (X1X3) was also observed. Similarly, in Equation (8), it can be noted that the energy consumption (EC) increases with pH0 (X1), I (X2), and Q (X3), which indicates that an increase in X1, X2, and (X3) is not beneficial on response EC. Also, the value of the coefficient of the unique interaction term (X1X2) is negative, which indicates that the interaction term results in beneficial on response EC. Furthermore, values of "Prob > F" less than 0.05 indicate that the model terms are significant. In the case of EM, the terms X1, X1 2 , X1X 2 2 (p-value = 0.0001, 0.0173, and 0.0015) are the statistically significant model terms. Meanwhile, for the case of EC the terms X1, X2, X1X 2 2 (p-value = 0.0029, 0.0066, and 0.0144) are the statistically significant model terms. Therefore, at this point, it can be said that pH0 and I are the operational variables with the most significant effect on response variables, EM and EC.
In addition, a perturbation plot (Figure 3) of the three tested operational variables (pH0, I, and Q), also revealed that the pH0 is the most significant factor on response EM, while the less significant factor was Q (Figure 3a). Also, it can be concluded from Figure 3b that the less significant factor on response EC was x3, i.e., Q, because the slope of EC is small, while the most significant factors on objective function EC were x1 and x2 because the slope of EC is high. The coefficients of the tested cubic models (Equations (7) and (8)) indicate the relative effect of the independent factors (X 1 , X 2 , and X 3 ) on responses (E M and E C ). On the basis of the coefficients in Equation (7), it can be noted that the mineralization efficiency (E M ) decreases with pH 0 (X 1 ), I (X 2 ), and Q (X 3 ). A positive effect of the interaction between the variables of pH 0 and I (X 1 X 2 ), and pH 0 and Q (X 1 X 3 ) was also observed. Similarly, in Equation (8), it can be noted that the energy consumption (E C ) increases with pH 0 (X 1 ), I (X 2 ), and Q (X 3 ), which indicates that an increase in X 1 , X 2 , and (X 3 ) is not beneficial on response E C . Also, the value of the coefficient of the unique interaction term (X 1 X 2 ) is negative, which indicates that the interaction term results in beneficial on response E C . Furthermore, values of "Prob > F" less than 0.05 indicate that the model terms are significant. In the case of E M, the terms X 1 , X 1 2 , X 1 X 2 2 (p-value = 0.0001, 0.0173, and 0.0015) are the statistically significant model terms. Meanwhile, for the case of E C the terms X 1 , X 2 , X 1 X 2 2 (p-value = 0.0029, 0.0066, and 0.0144) are the statistically significant model terms. Therefore, at this point, it can be said that pH 0 and I are the operational variables with the most significant effect on response variables, E M and E C . Table 5. ANOVA of the third-order models for E M (η 1 ) and E C (η 2 ). In addition, a perturbation plot (Figure 3) of the three tested operational variables (pH 0 , I, and Q), also revealed that the pH 0 is the most significant factor on response E M , while the less significant factor was Q (Figure 3a). Also, it can be concluded from Figure 3b that the less significant factor on response E C was x 3 , i.e., Q, because the slope of E C is small, while the most significant factors on objective function E C were x 1 and x 2 because the slope of E C is high.

Optimization for Mineralization Efficiency and Energy Comsumption
The determination of the optimal operational parameters to achieve the maximum mineralization of IBU with minimum specific energy consumption by applying a polynomial model of the responses (EM and EC) given by Equations (7) and (8) was assessed in Design-Expert ® V. 10 software. It is worth mentioning that the Design Expert Software performs the multivariable

Optimization for Mineralization Efficiency and Energy Comsumption
The determination of the optimal operational parameters to achieve the maximum mineralization of IBU with minimum specific energy consumption by applying a polynomial model of the responses (E M and E C ) given by Equations (7) and (8) was assessed in Design-Expert ® V. 10 software. It is worth mentioning that the Design Expert Software performs the multivariable optimization by using the Steepest Ascent method. The information entered to the software is given in Table 6. In order to conduct the optimization process, an objective for each factor and response must be selected from the software menu. This objective can be: maximize, minimize, target, within range, none (for responses only) and set to an exact value (factors only). Also, a minimum and a maximum limit must be provided for each parameter. In addition, a particular weight is assigned to each objective in order to adjust the shape of its particular desirability function. This is known as the importance of each objective and can be modified in relation to the other ones. The default for all objectives is that they are equally important and set as (+++). In this case, the importance was set based on the results described in Section 3.1. From the perturbation plot (Figure 3), it can be concluded that the volumetric flow rate (Q) does not exert a significant effect, thus Q can be set at a value of 1 L/min in the optimization criteria. This assumption (Q = 1 L/min) was made according to a previous work [25] because at this volumetric flow rate, the electrochemical flow reactor employed here has a high mass transport coefficient. Surface graphics (Figure 4b,d) are the most important graphical representation in the RSM. These graphics can be obtained by plotting Equations (7) and (8). Such graphics allow us to evaluate, from a qualitative point of view, the behavior of the whole studied system. The 3D surface graphs (Figure 4b,d) were plotted by varying two parameters (pH 0 and I) at a certain time while the third parameter is at a central value (volumetric flow rate of 1 L/min). These graphs were employed to evaluate the effects of interaction between operational parameters. The pH 0 and I interaction trajectories (Figure 4a,b) form a saddle area regarding pH 0 . This indicates that a pH 0 variation at a specific I, exerts a major effect on mineralization efficiency (E M ) in the studied region. The highest E M (89.5%) was obtained at high pH 0 with low E C . Although a relatively high E M was obtained at low pH 0 (Figure 4a), the specific energy consumption (E C ) was higher than E C at a higher pH 0 . Similarly, a high effect of the pH 0 and I interaction on specific energy consumption (Figure 4c,d) can be noted. A low E C was obtained at high pH 0 , although a relatively lower E C could be obtained at lower pH 0 , the results suggest working at high pH 0 because of desirability being 1 for both, E M and E C (Figure 4f). Also, in Figure 4a,c, saddle contour plots can be distinguished on the responses surfaces indicating that the interactions between the parameters are significant [39].  Figure 4e shows the feasible operational zone, which was plotted according to the constrained criteria (Table 6) of responses (E M and E C ). The optimal E M and E C were 89.5% and 4.32 kW h/g TOC, respectively, at an electrolysis time of 7 h. The black lines in the overlay plots are assembling the adopted constraints criteria, the area that fulfills the constraints is in yellow, and the region that does  Figure 4e shows the feasible operational zone, which was plotted according to the constrained criteria (Table 6) of responses (E M and E C ). The optimal E M and E C were 89.5% and 4.32 kW h/g TOC, respectively, at an electrolysis time of 7 h. The black lines in the overlay plots are assembling the adopted constraints criteria, the area that fulfills the constraints is in yellow, and the region that does not convene the constraints is in grey. The optimal region is enclosed by pH 0 (0-13) and I (2.60-4.40 A) at the electrolysis time of 7 h.
The multi-response optimization process has been assessed by the desirability function. The desirability function is defined in the range [0, 1]. The desirability function indicates if the objectives were reached, for example, values near to 1 indicate that all objectives were met. Meanwhile, values nearly to 0 indicate that some objectives were not succeeded [40]. In this work, the optimal region value has the overall desirability value of 0.9999993 indicating that all objectives were succeeded (Figure 4f). Also, the obtained desirability is classified as excellent and acceptable [41]. Furthermore, the responses (E M and E C ) have been simultaneously optimized using the developed models given by Equations (7) and (8).

Model Validation
The set of operating conditions with the highest value desirability was considered the optimum combination for required responses (E M and E C ). To validate the models, three complementary experiments were carried out by setting the optimal operating parameters computed with the Design-Expert ® V.10 software, namely pH 0 of 12.29, I of 3.26 A, and Q of 1 L/min for the initial total organic carbon of 35 mg TOC/L. At these optimal conditions, the IBU mineralization percentage and specific energy consumption were experimentally determined to be 91.6% and 4.36 KW h/g TOC, respectively. These values are in concordance to those given by models, 89.5% and 4.32 KW h/g TOC, respectively. The relative error between experimental and models were 2.3% and 0.9%, respectively. These results confirm that the developed models accurately describe the electrochemical mineralization of IBU on BDD electrodes (both cathode and anode) [3,23,24] and the specific energy consumption.
The associated cost of the electrolysis process was estimated by means of Equation (6) at the optimal operating conditions of the electrochemical mineralization of IBU. The electricity cost for industrial use in Mexico is of $2.806 MXP/kW h. This energy was supplied by the Mexican Federal Electricity Commission (CFE, Comisión Federal de Electricidad). Based on this cost, the corresponding price of the green mineralization of IBU was 0.002 US$/L ($0.035 MXP/L, taking into account that 1 US$/$20 MXP). Table 7 compares the results of this investigation with literature. The TOC removal percentage achieved in references (93.2%) [42] and (96%) [3] were greater than the TOC removal percentage (91.6%) achieved in this work. However, the volume treated (0.03 and 0.2 L, respectively) in literature was significantly smaller than the volume treated in this work (2.5 L). Additionally, the initial concentration of IBU (20 mg/L) in literature was lower than the initial concentration in this work (40 mg/L). Although, the volume (3.0 L) treated in reference [22] was greater than the volume treated in this work (2.5 L), the TOC removal (84%) achieved was lower than the TOC removal percentage (91.6%) achieved in this work. Furthermore, the specific energy consumption and associated cost (0.057 kW h/L and 0.003 US$/L, respectively) in reference [22] were higher than the specific energy consumption and associated cost (0.012 kW h/L and 0.002 US$/L, respectively) in this work. According to the obtained results of the green treatment used in this investigation, it can be concluded that this process is suitable for the elimination of emerging contaminants and specifically for IBU removal.

Kinetics of IBU Mineralization
To determine the kinetic order of the electrochemical mineralization of IBU, an additional experiment was performed under the optimal operating conditions found in this investigation. Figure 5 depicts the kinetic behavior of the mineralization of IBU. TOC decay fitting was found satisfactory with a pseudo-zero order kinetics, −dC TOC /dt = k 0 , where k 0 is the pseudo-zero-order rate constant. From this analysis, the k 0 value TOC removal is 0.0824 mg TOC/L min. This performance indicates a constant production of hydroxyl radicals. In Equation (9), M is an electroactive site of BDD anode where the hydroxyl radicals are formed by the anodic oxidation of water (Equation (10)) [43], , ,  and ne are stoichiometric coefficients.
Equation (9) is the global mineralization reaction: 22 The appearance of intermediate compounds that are also being oxidized by hydroxyl radicals  In Equation (9), M is an electroactive site of BDD anode where the hydroxyl radicals are formed by the anodic oxidation of water (Equation (10)) [43], φ, γ, δ and n e are stoichiometric coefficients. Equation (9) is the global mineralization reaction: The appearance of intermediate compounds that are also being oxidized by hydroxyl radicals attack is expected, however. By this means, two plausible mineralization routes have been proposed [42]. In any of these two proposed reaction routes, the first step is the hydroxylation of IBU albeit at different carbon positions. In both routes, the degradation of the intermediates occurs by further hydroxylation and decarboxylation until carboxylic acids are produced and these are further degraded down to CO 2 and water by • OH attack: To prove that the electrochemical mineralization of IBU was carried out by diffusion control (mass transfer from the bulk solution to the surface of the electrode), the relative magnitude of limiting current density J Lim , as seen in Equations (11) and (12), and applied current density (J Appl ) [4] can be compared. If J Appl < J Lim , the electrochemical process is currently controlled otherwise the electrochemical process is controlled by diffusion: where n e is the number of electrons, F is the Faraday constant, k m is the average mass transfer coefficient, C 0 is the initial concentration of IBU, A is the electrode area, and V s is the total volume of treated synthetic solution in batch mode. The value of the mass transfer coefficient k m was of 2.22 × 10 −6 m/s. Also, the J Appl value (109.0 mA/cm 2 ) was greater than J Lim value (2.74 mA/cm 2 ). Hence, the greener process employed in this investigation was controlled by diffusion because has a higher diffusion rate and higher mineralization efficiency of IBU [12], which implies that the diffusive flux is directly proportional to the steepness of the concentration gradient.

Conclusions
In this work, the electrochemical mineralization of IBU was successfully carried out with two BDD electrodes (both cathode and anode) in an electrochemical flow reactor (EFR) under recirculation batch mode.
The optimization of operational variables was successfully achieved through numerical optimization based on DOE. The maximum mineralization efficiency (E M ) was 91.6% with a minimum specific energy consumption (E C ) of 4.36 KW h/(g TOC). These values were achieved when EFR operates under a pH 0 of 12.29, I of 3.26 A, and Q of 1 L/min at an electrolysis time of 7 h.
The mathematical models developed in this work allow the prediction of E M and E C as a function of pH 0 , I, and Q under-tested experimental conditions. Additionally, the most significant factors were found to be pH 0 and I. These models are: BDD electrodes (both cathode and anode) allow one to conduct IBU mineralization with a relatively low energy consumption (4.36 KW h/g TOC). This offers the advantage of using sustainable power energy, i.e., solar batteries. Thus, the studied process here is a green treatment to eliminate emerging contaminants from wastewater.