Development and application of a water temperature related physiologically based pharmacokinetic model for enrofloxacin and its metabolite ciprofloxacin in rainbow trout

Introduction

World production of farmed aquatic animals is still the fastest-growing animal food-producing sector, which accounted for approximately 46% of the total fish source food supply ( 1 ). Rainbow trout is a minor species but with a relatively high worldwide consumption ( 2 ). In North China, turbot has become a vital aquaculture species ( 3 ). However, because of the high rearing density, fish are suffering from some severe infections by some pathogens, such as Aeromonas hydrophila, Vibrio anguillarum, Aeromonas salmonicida, Lactococcus garvieae, Pseudomonas spp., Flavobacterium psychrophilum , and Yersinia ruckeri ( 4 – 8 ). The infections may lead to severe mortality among trout and substantial financial losses for the trout industry. It is of great importance to treat infections with effective antibacterials.

Enrofloxacin (ENR) is a synthetic fluoroquinolone developed especially for veterinary application, and it acts by inhibition of bacterial DNA-gyrase ( 9 ). ENR has been demonstrated effective against all common aquatic pathogens mentioned above ( 10 – 13 ). It can be in vivo biotransformed to its metabolite ciprofloxacin (CIP) ( 13 , 14 ), which has been extensively used in the human clinic for the last two decades. In China, ENR has been licensed for aquatic medical use, and its recommended doses were 10 to 20 mg/kg B. W. per day for 5 to 7 days, administered through mixing with the formulated feed ( 15 ). The official withdrawal period for ENR in aquaculture was 500 degree-days ( 15 ). In some other countries, bath dosing was also approved for ENR in aquaculture; however, the recommended doses varied among different counties ( 16 , 17 ). In the United States (US) and the European Union (EU), the unregistered compounds (such as ENR) were approved to treat fish diseases in an extra-label manner. Under these circumstances, a standard withdrawal period (500 degree-days) has been imposed for these off-label compounds ( 18 ). Unlike the withdrawal periods in mammals, those in fish will be significantly affected by the water temperature because fish are heterothermic animals ( 19 ). Therefore, the drug withdrawal periods will dramatically vary at different water temperatures even under the same dosing schedule in fish.

In China, marker residue for ENR is the sum of ENR and CIP with a maximum residue limit (MRL) of 100 μg/kg in muscle plus skin ( 15 ). However, the official withdrawal period was not available for ENR in aquaculture animals in China. To our knowledge, the residue of ENR and its metabolite CIP in edible tissues from rainbow trout is relatively typical compared with the other antibacterials ( 16 , 20 ). In Iran, the total concentration of ENR and CIP in rainbow trout edible tissue exceeded the MRL (100 μg/kg) by at least 18. 92% of the collected sample ( n = 74) ( 20 ). Similar results have also been found in other countries ( 16 ). Excessive residues of antibiotics in fish tissues may lead to adverse effects on human health ( 21 ). Allergic reactions, gastrointestinal disturbances, carcinogenic effects, and photosensitivity constituted direct toxic effects ( 16 ). In addition to the direct toxic effects, consumers are more worried about the prevalence of antibiotic resistance through selective pressure on bacteria ( 22 ). A study conducted in rats has indicated that ENR had some acute toxic effects, including reducing body weight gain, caecal distension, degenerative changes in the knee joint, and the testicular effects in male subjects ( 23 ). These results showed that it is essential to monitor the residues of ENR and related compounds in foods of animal origin.

There have been increasing studies on predicting veterinary drug residues ( 24 – 27 ) and drug withdrawal periods ( 21 , 28 – 31 ) based on the PBPK model. The PBPK model is based on the mass balance equation and allows the application of population variability data and in vitro mechanism to predict drug concentration in edible tissues ( 32 ). Some models have been developed in rainbow trout for environmental pollutants ( 33 – 36 ), rather than veterinary drugs. Also, neither of those previous models investigated the impact of water temperature on the compound disposition. Considering the wide range of climatic zones in which trout have been cultivated, it is important to develop a water temperature related PBPK model containing both ENR and its metabolite CIP to forecast tissue residues in trout. The objectives of the current study were (i) to establish and validate a water temperature related PBPK model containing both ENR and CIP in rainbow trout; (ii) to forecast the tissue residues and the withdrawal periods for ENR at different water temperatures based on this model.

Materials and Methods

Concentrations vs. Time Data of ENR and CIP

The published studies regarding ENR and rainbow trout have been widely searched, and the pharmacokinetics or depletion studies conducted in rainbow trout after intravenous (IV), oral (PO), or bath administration (IB) were chosen. The concentrations of ENR and CIP in plasma, serum, and tissue were read directly or extracted from the previously published figures using the software of GetData Graph Digitizer (version 2. 26). The key information is given in Table 1 about those selected studies.

TABLE 1

Literature used in the model optimization and validation.

Model Structure

The current PBPK model contained ENR and its metabolite CIP sub-models connected through hepatic metabolism. The sub-model of ENR had 10 compartments, including the digestive tract (stomach and intestine), liver, kidney, muscle, skin, gill, venous blood, arterial blood, and a virtual compartment representing the rest of the body ( Figure 1 ). Compared with the ENR sub-model, the stomach and intestine were not incorporated in the CIP sub-model ( Figure 1 ). As PO and IB are the approved administration routes for ENR in rainbow trout, they were both included in the present ENR sub-model. Additionally, the IV injection was also incorporated into the ENR sub-model to determine the same distribution and elimination profiles under all three administration routes. A compartment representing culture water was applied to simulate drug absorption after IB administration. An enterohepatic circulation module for ENR was initially included in this model; however, that module could not increase the accuracy of the prediction and even reduced the prediction accuracy for ENR and CIP concentrations in the liver (data not shown here). Therefore, the it was not finally included in the present study. Based on the previous PBPK models for other quinolones ( 28 , 29 , 40 ), flow-limited compartments were used for both ENR and CIP in the present study. The present PBPK model was developed based on the software platform of acslXtreme (version 3. 0. 2. 1). The entire code for this model is provided in the Supplementary Materials .

FIGURE 1

A schematic diagram of the current PBPK model for ENR and CIP in rainbow trout. Q _x (L/h) is blood flow through some tissue. A specific tissue was distinguished by its subscript x, and tissues of kidney, muscle, skin, gut, liver, and the rest of the body compartment were abbreviated as k, m, s, g, l, and r, respectively. Q _tot is the cardiac output, indicating that all cardiac output flows through the gill. Three dosing routes (IV, IB, and PO) were included in the model. The abbreviations of IV and PO are all ENR doses intravenously and orally administrated to rainbow trout, respectively. The symbol of IB represents total exposure through an immersion bath. After IV dosing, ENR enters into the venous blood completely and directly. Following PO administration, the drugs directly enter the stomach and then enter the small intestine under the action of gastric emptying, where some of them are absorbed into the blood circulation. Those unabsorbed drugs are eliminated from the fish body to the culture water. K _st (h ⁻¹ ) is the rate constant of gastric emptying, K _aPO (h ⁻¹ ) is the rate constant of absorption, and K _guc (h ⁻¹ ) is the rate constant of elimination with feces. F represents oral bioavailability. During the immersion bath, ENR is absorbed into the venous blood through the gill with the absorption rate constant of K _aIB (h ⁻¹ ). From gill to water, another distribution rate constant is K _gw (h ⁻¹ ). ENR circulates to various tissues with the blood and is eliminated by liver metabolism and renal excretion. K _f (h ⁻¹ ) is the metabolism rate constant, and Cl _re (L/h/kg) is the renal clearance of ENR. When CIP is bio-transformed from ENR, it also circulates to various tissues. Then it is further eliminated by renal excretion, and the renal clearance for CIP is Cl _mre (L/h/kg). ENR and CIP in the fish body are all excreted into the water; however, the CIP concentrations were not predicted because of their low levels. ENR in water has a degradation rate constant, K _de (h ⁻¹ ).

For the IV route, ENR was directly injected into venous blood at the IV dose (mg/kg b. w.) and the duration of the infusion period (timeiv) was set as 0. 001 h ( 41 ). For the IB route, the initial concentration of ENR in the water was 20 and 100 ppm, and the exposure periods (timeib) were 2. 5 and 0. 5 h, respectively ( 38 ). During the immersion bath, the drug was assumed to be only absorbed from the gill to the blood circulation, with the absorption rate constant of K _aIB and a complete 100% absorption ( Figure 1 ). For the PO route, a two-compartment model including stomach and gut was applied to simulate the absorption based on our previous study ( 26 ). It was assumed that ENR entered the stomach directly and then was transported into the gut through gastric emptying at the rate of K _st . Once in the intestine, most ENR will be absorbed with a rate constant of K _aPO , and the bioavailability was 66. 13% ( 3 ). Those unabsorbed drugs will be excreted from the intestinal contents with the feces into the culture water ( Figure 1 ). And the excretion rate was abbreviated as K _guc .

Following IV injection or extravascular absorption, ENR was distributed through the bloodstream to all tissue compartments. As reported anywhere ( 26 , 28 , 29 , 41 ), the mass balance equations were coded to describe the concentration or mass change for ENR or CIP in each compartment ( Table 2 ). According to the previous report ( 23 ), ENR is mainly eliminated by liver metabolism and renal excretion. Therefore, parameters of K _f and Cl _re were applied to simulate both processes, respectively. K _f was the rate constant of biotransformation from ENR to CIP in liver and Cl _re was an abbreviation for ENR renal clearance. The drugs excreted by the kidneys directly entered the aquaculture water ( Figure 1 ). Besides the intestinal and renal excretions, some ENR was directly excreted from the gill to the aquaculture water, and the excretion rate constant was K _gw ( Figure 1 ).

TABLE 2

Differential equation describing the change rate of ENR and CIP concentrations (mol/L) or mass (mol) in each compartment.

After biotransformation, CIP was gradually distributed to the other tissues through the bloodstream. Since the primary elimination route of CIP was via urine ( 23 ), CIP was assumed to be eliminated only through renal excretion, and the parameter of Cl _mre (abbreviation for renal clearance) was used to simulate this process. Because of the low levels of CIP in tissues and aquaculture water after ENR administration ( 38 , 39 ), we did not simulate the CIP concentrations in the aquaculture water. More details on the equations simulating the ENR and CIP dispositions could be found in Table 2 and the model code presented in the Supplementary Materials .

Model Parameterization

It is worth emphasizing that all common parameters included in different dosing route models, such as Cl _re , Cl _mre , K _f , etc., shared their same values. Since both serum and plasma concentrations previously reported ( Table 1 ) were used to optimize and validate the current model, the parameters of pre and hematocrit (pcv) were used to calculate the ratios of serum and plasma to the total volume of whole blood, respectively. The pre and pcv values were set as 55. 5 and 30. 4%, respectively ( 42 ). To simplify the current simulation, neither ENR nor CIP was assumed to enter blood cells, and the amount of each compound in blood was equal to the amount in plasma or serum.

The model parameters, including blood flow (Q _cx ), tissue weight (V _cx ), and the partition coefficients between tissue and plasma for both ENR and CIP (abbreviated as P _x and P _mx , respectively), are presented in Table 3 . The parameters for tissue weight were derived from previous PBPK models in rainbow trout ( 33 ), crucian carp ( 24 ), and grass carp ( 25 ). The blood flow parameters were also derived from previous PBPK models in fish ( 24 , 33 ). Tissue weight and blood flow were expressed as fractions of body weight (b. w.) and total cardiac output, respectively ( Table 3 ). Because the mean body weights were varied among the trout in the previous studies ( Table 1 ), the current model was adjusted based on the specific b. w. reported in each study. According to a previous report ( 42 ), the water temperature significantly affected the cardiac output of rainbow trout. And the cardiac output was estimated based on the following linear equation between water temperature (Temp, °C) and total cardiac output (CO, ml/min/kg): CO= Temp × 3. 95–12. 9 ( 42 ). Partition coefficients for ENR were calculated according to the area method ( 43 ), based on the ENR concentrations in plasma and tissues derived from a previous report ( 38 ). Three dosage regimens were applied in that study. Therefore, we calculated the P _x values based on the average AUC values. It was assumed that the P _mx values in the tissues of muscle, skin, gut, liver, and kidney in rainbow trout were equal to those reported in humans ( 40 ). Those in the other compartments (gill and the rest compartment) were optimized through a maximum likelihood algorithm of Nelder-Mead based on the previously reported concentrations of CIP in serum, muscle, and liver ( 13 ). In addition to P _mgi and P _mr , the values of P _gi and P _r were also obtained through parameter optimization. More details about the optimization process could be found below.

TABLE 3

Parameters of tissue weights, blood flows, and tissue/plasma partition coefficients used in this physiologically based pharmacokinetic model.

In addition to some partition coefficients for ENR and CIP mentioned above, some other parameters were unavailable. Therefore, their values were also optimized based on the published ENR and CIP concentrations ( Table 1 ). It should be noted that all optimizations were performed in acslXtreme through the Nelder-Mead algorithm. During optimization, those ENR concentrations in plasma after IV dosing ( 37 ) were initially applied to optimize the parameters included by three different routes of the model, including P _gi , P _r , K _f , and Cl _re . After obtaining final values of these parameters were, the plasma concentrations of ENR ( Table 1 ) published by the others ( 3 ) were used to validate these parameter values through visual comparisons of the predictions and observations. If most predicted concentrations were consistent with those published ones, these optimized values were determined. Next, the other parameters only used in the PO model were optimized through the published ENR concentrations in plasma and tissues ( 3 ), including K _st , K _aPO , and K _guc . The other concentration data reported in plasma, serum, or tissues ( Table 1 ) were used to validate these optimized values. Like the PO model, the parameters of K _aIB , K _gw , and K _de used in the IB model were next optimized based on the published ENR concentrations ( 38 ). The other published concentrations ( Table 1 ) were used for the validation of these optimizations.

When these parameters for ENR were determined, the published ENR and CIP concentrations following PO dosing at different water temperatures ( Table 1 ) were applied to optimize the parameters for CIP used in all routes of the model, including P _mr , P _mgi , and Cl _mre . And the other concentrations of ENR and CIP were utilized to verify these optimizations ( Table 1 ). Till this moment, all the model parameters were determined and fixed. Please note that all simulations were adjusted according to the administration routes and dosage, fish b. w., and water temperatures used in those previous studies; additionally, each validation was carried out immediately after the corresponding optimization.

Model Validation

The current model was validated by visual comparisons of the present predictions and the previous observations. It should be emphasized that all of those observations for validations were not used in the optimization process. Linear regression analysis with the determination coefficient was also performed to validate this model. According to a previous study ( 31 ), a determination coefficient > 0. 75 is regarded as a general criterion for good prediction. Also, the mean absolute percentage error (MAPE) was calculated to validate this model ( 41 ). The evaluation criteria of MAPE are: (i) excellent prediction: MAPE < 10%; (ii) good prediction: 10% < MAPE < 20%; and (iii) acceptable prediction: MAPE < 50% ( 26 ).

Sensitivity Analysis

A sensitivity analysis was carried out according to the previous study ( 41 ). In the sensitivity analysis process, the central difference method was utilized; more details could be found in our previous studies ( 26 , 41 ). If the absolute value of its NSC was > 0. 25 ( 41 ), this parameter was considered as an influential one. In order to simultaneously perform the sensitivity analysis on all parameters, three routes of administration were simulated simultaneously. The PO and IV doses were simulated at 10 mg/kg b. w., while for the IB route, the exposure concentrations and time in water were 10 ppm and 1 h, respectively.

Monte Carlo Analysis

Up to 48 parameters were included in the current model. Due to the computational complexity, it was impossible to perform a Monte Carlo simulation for all parameters. Therefore, a Monte Carlo analysis was only performed on the influential parameters (see the above sensitivity analysis for details). Their central tendency and spread, expressed as mean and standard deviation respectively, were from the previous studies ( 3 , 13 , 24 , 25 , 37 – 40 ) or obtained by parameter optimization (see the model parameterization above for details). Because of the scarcity of SD values for some influential parameters, their SD values were set to be 10% of their mean values. Normal distribution was assumed for these parameters, and their average, standard deviation (SD), lower limit (Mean-SD), and upper limit (Mean + SD) are presented in Supplementary Table 1 . Only ENR orally administered was approved for aquacultural application in China; therefore, single and multiple oral dosing were simulated by the Monte Carlo analysis. In addition to oral administration, IB dosing was also commonly applied in aquatic clinics. Therefore, a Monte Carlo analysis was also performed for IB exposure. In order to determine the temperature effects, three different water temperatures (5, 10, and 16°C) were simulated in each analysis. All these analyses were undertaken through the Monte Carlo wizard in the acslXtreme software. And each Monte Carlo analysis contained 500 iterations.

Withdrawal Interval Estimation

A 500-iteration Monte Carlo analysis was included in the current model, and different dosage regimens were simulated (see the Monte Carlo analysis listed above). After every run, the predicted concentrations of ENR, CIP, and ENR plus CIP vs. time data were all automatically recorded by acslXtreme. When all 500 runs were finished, it was equivalent to obtaining the concentration-time data in 500 virtual individuals. These data were used to calculate the withdrawal interval in each individual further to ensure the predictions below the corresponding MRL for each individual ( 41 ). According to the guidance of CCVP ( 15 ), a 99th percentile was used for withdrawal interval calculation. The M-type code for withdrawal interval estimation is presented in the Supplementary Materials . The residue target tissue in fish approved for ENR in China was muscle and skin in natural proportions; however, a previous study indicated that the ENR residue seemed to be especially bound to fish skin ( 44 ). Therefore, we divided the skin and muscle into two separate compartments in the current model and calculated the withdrawal periods in both of them. More details about the withdrawal interval calculation can be found in the Supplementary Materials or our previous study ( 41 ).

Results

Model Parameters

The anatomical and physiological parameter values used here were derived from previous models ( 24 , 25 , 33 ) and are listed in Table 3 . The partition coefficient for ENR were calculated based on the area method ( 43 ), and their final values were 4. 9, 11. 53, 2. 83, 7. 38, and 4. 88 in the liver, kidney, muscle, skin, and gut, respectively. Partition coefficients for ENR in gills and the rest of the body were obtained by parameter optimization, and their final values were 3. 46 and 0. 13, respectively. Partition coefficient values for CIP were assumed to be equal to those previously used in humans ( 40 ), with their final values of 3. 67, 8. 2, 1. 6, 0. 718, and 3. 39 in the liver, kidney, muscle, skin, and gut, respectively. Similar to P _gi and P _r , the values of P _mgi and P _mr were also acquired by parameter optimization with the final values of 2. 45 and 0. 15, respectively. The parameters related to absorption after PO or IB administration were also determined through optimization, whose final values were 0. 175 h ⁻¹ , 0. 052 h ⁻¹ , 1. 103 h ⁻¹ for K _st , K _aPO , and K _aIB , respectively ( Table 4 ). The parameters related to the eliminations of ENR or CIP were also obtained through optimization, whose values were 0. 0725 h ⁻¹ , 0. 058 L/kg/h, 0. 605 h ⁻¹ , 0. 061 h ⁻¹ , 12003. 310 h ⁻¹ , and 116. 14 L/kg/h for K _f , Cl _re , K _guc , K _gw , K _de , and Cl _mre , respectively.

TABLE 4

The results of parameters optimization used under all routes administration based on the published concentrations after intravenous injection.

Model Validation

This model was validated through the visual comparison between the predicted and published concentrations of ENR in tissues/plasma or CIP in the liver, and the comparison results are shown in Figures 2 – 7 . As demonstrated by these figures, those published ENR and CIP concentrations in plasma, serum, and tissues were all well-predicted after three different routes of administration and at different water temperatures. At the same time points, most predictions are very close to the reported concentrations ( Figures 2 – 7 ). However, the CIP concentrations in the liver were overestimated by ~1. 5 times, especially at the later sampling time points ( Figure 5 ). This inconsistency might be because there were not enough published CIP concentration data for parameter optimization ( Table 1 ). In the previous studies ( 3 , 9 , 13 ), the concentrations of CIP were usually irregular after different routes administration of ENR. Besides visual comparisons, the linear regression analysis was also undertaken between the predicted and published concentrations ( Table 5 ). The current model was proved to be generally acceptable since most of the determination coefficients were above 0. 75 except for some individual ones lower than (but very close to) 0. 75. The smallest coefficient of determination (0. 035) was determined for ENR concentrations in the liver ( Table 5 ). The MAPE values were also calculated to evaluate the current model, and the results were similar to visual comparisons and linear regression analysis. The MAPE values ranged from 3. 2 to 61%, and only four values > 50% ( Table 5 ). All these validation results confirmed that the present prediction results were acceptable.

FIGURE 2

Comparisons between the predicted (curves) and published [points; ( 3 )] ENR concentrations (μg/ml) in plasma after a single IV dose at 10 mg/kg b. w. in rainbow trout reared at the water temperature of 16°C.

FIGURE 3

Comparisons between the predicted (curves) and published [points; ( 37 )] ENR concentrations (μg/ml) in serum after different single PO doses in rainbow trout reared at two different water temperatures [(A), at 10°C;(B), at 15°C].

FIGURE 4

Comparisons between the predicted (curves) and published [points; ( 38 )] ENR concentrations (μg/ml or μg/g) in trout plasma and tissues after an immersion bath in water with ENR concentration at 20 ppm for 2. 5 h. The rainbow trout were reared at the water temperature of 16. 3°C.

FIGURE 5

Comparisons between the predicted (curves) and published [points; ( 39 )] CIP concentrations (μg/g) in the liver after a single oral dose of ENR at 30 mg/kg b. w. in rainbow trout reared at three different water temperature.

FIGURE 6

Comparisons between the predicted (curves) and published [points; ( 39 )] ENR concentrations (μg/ml or μg/g) in plasma and tissues after a single oral dose of ENR at 30 mg/kg b. w. in rainbow trout reared at two different water temperatures [(A), at 5°C;(B), at 10°C;(C), at 15°C].

FIGURE 7

Comparisons between the predicted (curves) and published [points; ( 38 )] ENR concentrations (μg/ml or μg/g) in plasma and tissues after a single oral dose of ENR at 10 mg/kg b. w. in rainbow trout reared at 16. 3°C.

TABLE 5

Results of linear regression analysis between the predictions and observations of ENR or CIP (μg/g or μg/ml) in tissues, plasma, and serum after different routes of administration in rainbow trout.

Sensitivity Analysis

The complete results of sensitivity analysis are presented in Supplementary Tables 2, 3 . A positive NSC value indicated a positive correlation between the parameter value and the AUC, while a negative NSC indicated an opposite relationship between them. It was shown that most of the parameters have similar impact extents on ENR or CIP AUCs in different tissues. However, the parameters of Q _ck , Q _cs , V _cs , P _l , P _k , P _s , and P _g only had positive impacts on the AUCs of ENR ( Supplementary Table 2 ). Similar positive influences on the CIP AUCs were observed for P _ml and P _mk ( Supplementary Table 3 ). The dosage of different routes and the volume of aquaculture water had the highest influences on both AUCs of ENR and CIP ( Supplementary Tables 2, 3 ) because these parameters directly represented the exposure doses of ENR. In addition to these exposure parameters, water temperature also had a more significant impact on the AUCs of ENR and CIP. This result was consistent with the blood flow limited mechanism because the cardiac output is proportional to water temperature ( 42 ).

Monte Carlo Analysis and Withdrawal Interval Estimation

Monte Carlo analysis was only performed on the influential parameters ( Supplementary Table 1 ). ENR and CIP concentrations and their total residues after one single PO administration of ENR at 10 mg/kg b. w. were predicted according to each Monte Carlo run. Results are shown in Supplementary Figures 1–9 . Oral multiple-dose were also simulated. However, only the predicted concentrations at 16°C are shown in Supplementary Figures 10–12 . In addition to PO administration, two immersion baths were also simulated at three different water temperatures; however, only the results at 16°C are shown in Supplementary Figures 13–18 . Based on these predicted results, the withdrawal intervals were determined to ensure that the sum of ENR and CIP concentrations in the 99th percentile of the population (at least 495 virtual individuals) were below the corresponding MRLs.

The distributions of withdrawal intervals at different water temperatures were compared, and the results after multiple oral doses are shown in Figure 8 as examples. Those under the other dosage regimens could be found in the Supplementary Materials ( Supplementary Figures 19, 20 ). Also, the comparison result of withdrawal intervals under different dosage regimens and water temperatures are presented in Table 6 . Under the same conditions, the withdrawal interval in the skin was indeed longer than that in the muscle. The maximum difference between the two was 6 days, and the minimum was 2 days ( Table 6 ). The present findings were consistent with the previous report ( 44 ). We also translated the unit of withdrawal interval under different dosage regimens from days to degree-days by multiplying the drug withdrawal interval in days by the corresponding water temperature. Their corresponding results were all shorter than the official withdrawal period in China (500 degree-days).

FIGURE 8

Distributions of withdrawal intervals in the muscle(A)and skin(B)after repeated oral dosing of ENR (20 mg/kg b. w. per day for 7 consecutive days) based on the Monte Carlo analysis. Notes: the arrows represented the 99th percentiles of the distribution at three different water temperatures.

TABLE 6

Comparison of the withdrawal intervals under different dosage regimens calculated based on the current PBPK model.

Discussion

Compared with those previous PBPK models in fish species ( 24 , 25 , 33 ), the present is the first one related to the water temperature. Unlike mammals, fish are heterothermic. The water temperature has a significant effect on the elimination of drugs from fish ( 19 ). Therefore, a PBPK model related to the water temperature will be of great significance. The validation results indicated that the present model could accurately predict the ENR and CIP concentrations in the water temperature range of 5°C to16°C. In the current model, three administration routes were simulated, containing PO, IB, and IV dosing. The first two routes were labeled by the regulatory authorities. The third one, although unapproved, was also simulated to optimize and validate the current model. In order to simulate the IB route, the aquaculture water was incorporated into the present model. Following the IB exposure, ENR was absorbed into the fish body from the water; after the distribution and metabolism, they were eventually excreted into the water underwent final degradation there. As the marker residue for ENR, parent compound and CIP were both simulated, and they were linked through the hepatic metabolism. The parameter of K _f was used to simulate the hepatic metabolism of ENR, and its final value (0. 0725 h ⁻¹ ) was obtained by optimization. In the optimization process, the setting of the initial value is a key step. We initially conducted an extensive literature search to obtain the initial value of this parameter in fish. Unfortunately, it was not available. Therefore, we finally set it as 0. 02 h ⁻¹ . Some further studies, such as in vitro or in vivo metabolism experiments, should be carried out to validate these initial and final values for K _f .

Monte Carlo simulation containing 500 iterations was included in this model to generate a population of 500 virtual individuals and to predict the drug concentrations in the population further. Based on these predicted concentrations, the withdrawal intervals were estimated and compared for different water temperatures. Compared with the conventional animal experiment method to calculate the drug withdrawal period, the PBPK model incorporating Monte Carlo simulation has three significant advantages. First, the PBPK model is predictive rather than descriptive, and its results are more accurate. Second, Monte Carlo simulation is not limited by the number of animals, and can fully take into account the variation between individual animals. Finally, the PBPK model can obtain a withdrawal interval closer to the clinical reality by changing the physiological parameters in the pathological state.

In the current model, most anatomical and physiological parameters in rainbow trout were from some previous fish models ( 24 , 25 , 33 ). It was found that all these parameters were valid because the present model had good predictions in most tissues after three routes of dosing. In addition to these parameters, the partition coefficients for ENR were determined by the area method ( 43 ). Those for CIP were assumed to be equal to the humans model ( 40 ). The final values of ENR partition coefficients ranged from 2. 83 in muscle to 11. 53 in the kidney ( Table 3 ), and the corresponding values for CIP ranged from 0. 718 in the skin to 8. 2 in the kidney ( Table 3 ). These results indicated that the kidney was a primary elimination organ for both ENR and CIP, consistent with the previous study ( 23 ). Parameters values regarding to extravascular absorption were acquired through parameter optimization. And the values of K _st , K _aPO , and K _aIB were 0. 175, 0. 052, and 1. 103, respectively ( Table 4 ). These results showed that ENR had a relatively quicker absorption following an immersion bath, which might be related to the structure of the current model. Following IB exposure, the ENR was directly absorbed into gills from the aquaculture water, while after PO dosing, ENR firstly entered the stomach and could only be absorbed after entering the intestine under the action of gastric emptying. The parameters interrelated to the elimination of ENR were also obtained through optimization, and the values of K _f , Cl _re , K _guc , and K _gw were 0. 0725 h ⁻¹ , 0. 058 L/kg/h, 0. 605 h ⁻¹ , and 0. 061 h ⁻¹ , respectively ( Table 4 ). These parameter values indicated that the renal and intestinal excretions for ENR were more critical than the biotransformation, which was also consistent with the fact that the CIP concentrations were much lower than those of ENR after different routes administration of ENR ( 3 , 37 , 38 ). CIP had a quicker elimination than ENR with a Cl _mre of 116. 14 L/h/kg.

Water temperature has a significant effect on the drug disposition in the fish body ( 19 ), for two main reasons. First, water temperature significantly affects the cardiac output, distribution of blood flow, and local perfusion in different tissues ( 42 ). Like ENR, the distributions of most drugs are restricted by the blood flow rate. Second, as heterothermic animals, fish cannot control their body temperature. It is well-known that lower temperatures can reduce the activity of metabolic enzymes, thereby slowing down the rate of metabolic reactions. Therefore, the water temperature will affect the distribution and metabolism of drugs in fish. In this model, we use the relationship between water temperature and cardiac output previously reported by other researchers ( 42 ) to estimate the temperature effects on drug disposition. We have also tried to incorporate the impact of water temperature on ENR metabolism in the model. However, a previous study showed that water temperature had little effect on the ENR tissues concentrations in rainbow trout, and only slightly affected ENR concentration in plasma ( 39 ). Also, the expression amount of CYP3A in rainbow trout liver cells did not differ significantly at three different temperatures (5, 10, and 15°C) ( 39 ). Therefore, in the current model, the water temperature was only linked to cardiac output ( Table 2 ).

There are several limitations to the current study. The first one is related to the optimization of parameters related to drug absorption and elimination. Because of the abundance of ENR and CIP concentration data after different routes of administration in rainbow trout, we did not carry out relevant experiments to obtain these parameter values but obtained them through parameter optimization based on those published concentration data. Whilst this is not necessarily incorrect, more studies should be further performed to validate these parameter values. The second limitation pertains to the aquaculture water compartment. Although the culture water compartment was included in the current model, neither ENR nor CIP concentrations were predicted or validated in the water. This is mainly because the volume of aquaculture water was not available in the previous studies ( 2 , 3 , 37 , 39 ), so it is impossible to predict the drug concentration in the water. Also, this study aimed to predict drug concentrations in edible tissues to reduce residual risk of ENR and CIP. Therefore, the water concentrations were not expected here. Thirdly, the predicted concentrations, such as ENR and CIP concentrations in the gill, CIP concentration in tissues other than the liver, were not validated because of the scarcity of observations. In the present model, the gill is a bridge connecting venous and arterial blood. More importantly, gill is also the main route of drug absorption after IB exposure. In order to improve this limitation, some depletion studies of ENR following different routes of administration and at different water temperatures should be further performed to obtain the ENR and CIP concentrations in different tissues to validate the current model. Fourthly, the age of rainbow trout was not taken into account, which might affect the metabolism of ENR. The withdrawal time of enrofloxacin at different water temperatures for different administration routes varied from 8 to 36 days ( Table 6 ). While the maximum recorded lifespan for a rainbow trout was up to 11 years. Therefore, we have reason to believe that a withdrawal period of 38 days may not have any significant effect on ENR metabolism during the lifespan. Finally, the partition coefficients for CIP were assumed to be the same as those for humans. This is a major assumption that could be erroneous due to differences in the phospholipid and protein composition of tissues between humans and fish. However, because the concentration data of CIP in rainbow trout tissue were relatively scarce, we used those available concentration data to optimize and validate the model, rather than to calculate the partition coefficients for CIP. Some depletion studies should be further performed to validate these partition coefficients for CIP.

The withdrawal intervals were estimated and compared at different water temperatures based on this model ( Table 5 ). Under different dosage regimens, all withdrawal intervals at low water temperatures were longer than those at high water temperatures. This was an obvious fact, and its reason stemmed from the influence mentioned above of water temperature on the cardiac output. It should be noted that the withdrawal intervals estimated here, ranging from 80 to 272 degree-days ( Table 5 ), were all shorter than the labeled one in China (500 degree-days). The officially approved target tissue for ENR residue was muscle and skin in natural proportions in fish species. However, the skin and muscle were separated in the present model because a previous study showed that ENR seemed to be especially bound to fish skin ( 44 ). Our predicted results indeed proved this specific binding ( Table 5 ). Therefore, the present results might encourage the regulatory authorities to shorten the official withdrawal period for ENR in rainbow trout.

Conclusion

In conclusion, the current model can adequately predict ENR and CIP concentrations following three routes of dosing in rainbow trout reared at a wide range of water temperatures (5–16°C). The Monte Carlo analysis was included in the model to predict tissue depletion in a population containing 500 virtual individuals and to further determine the withdrawal intervals for ENR in rainbow trout at three different water temperatures. This research provides a basis for application the temperature-related PBPK model to predict residue concentrations and further estimate the withdrawal intervals at different water temperatures. This model also can be further used for a risk assessment for some water pollutants.

Data Availability Statement

The original contributions presented in the study are included in the article/ Supplementary Materials , further inquiries can be directed to the corresponding author/s.

Ethics Statement

Ethical review and approval was not required for the animal study because this was a modeling study, and no animal experiments were involved in this study.

Author Contributions

FanY conceived this project. FangY and C-SZ did the citation research. DW, HW, and Z-WS extracted and collected all the concentration-time data. H-TS and MZ collected the physiological and anatomical parameters for rainbow trout. FanY developed and optimized this model with support from M-LY and YZ. FanY wrote the manuscript with the backing from FangY, C-SZ, and HW. All authors read and approved this final manuscript.

Funding

This study was financially supported by Natural Science Foundation of Henan (Grant No. 212300410037) and National Natural Science Foundation of China (Grant No. 31402253).

Conflict of Interest

The authors declare that the research was conducted in the absence of any commercial or financial relationships that could be construed as a potential conflict of interest.

Supplementary Material

The Supplementary Material for this article can be found online at: https://www. frontiersin. org/articles/10. 3389/fvets. 2020. 608348/full#supplementary-material

References

1. FAO. The State of World Fisheries and Aquaculture 2020 . (2020). Available online at: www. fao. org/3/ca9229en/ca9229en. pdf (accessed September 10, 2020).

2. Lucchetti D, Fabrizi L, Guandalini E, Podesta E, Marvasi L, Zaghini A, et al. Long depletion time of enrofloxacin in rainbow trout ( Oncorhynchus mykiss ). Antimicrob Agents Chemother . (2004) 48: 3912–7. doi: 10. 1128/AAC. 48. 10. 3912-3917. 2004

3. Liang J, Li J, Zhao F, Liu P, Chang Z. Pharmacokinetics and tissue behavior of enrofloxacin and its metabolite ciprofloxacin in turbot Scophthalmus maximus at two water temperatures. Chin J Oceanol Limnol . (2012) 30: 644–53. doi: 10. 1007/s00343-012-1228-2

4. Fauzi IA, Haga Y, Kondo H, Hirono I, Satoh S. Dietary citrulline improves survival of rainbow trout Oncorhynchus mykiss juveniles challenged with Vibrio anguillarum . Aquaculture . (2020) 528: 735491. doi: 10. 1016/j. aquaculture. 2020. 735491

5. Kiadaliri M, Firouzbakhsh F, Deldar H. Effects of feeding with red algae ( Laurencia caspica ) hydroalcoholic extract on antioxidant defense, immune responses, and immune gene expression of kidney in rainbow trout ( Oncorhynchus mykiss ) infected with Aeromonas hydrophila . Aquaculture . (2020) 526: 735361. doi: 10. 1016/j. aquaculture. 2020. 735361

6. Bulfon C, Prearo M, Volpatti D, Byadgi O, Righetti M, Maniaci MG, et al. Resistant and susceptible rainbow trout ( Oncorhynchus mykiss ) lines show distinctive immune response to Lactococcus garvieae . Fish Shellfish Immunol . (2020) 105: 457–68. doi: 10. 1016/j. fsi. 2020. 06. 040

7. Samuelsen OB. Pharmacokinetics of quinolones in fish: a review. Aquaculture . (2006) 255: 55–75. doi: 10. 1016/j. aquaculture. 2005. 12. 008

8. Quesada SP, Paschoal JAR, Reyes FGR. Considerations on the aquaculture development and on the use of veterinary drugs: special issue for fluoroquinolones-a Review. J Food Sci . (2013) 78: R1321-R1333. doi: 10. 1111/1750-3841. 12222

9. Yang F, Kang J, Yang F, Zhao Z, Kong T, Zeng Z. Preparation and evaluation of enrofloxacin microspheres and tissue distribution in rats. J Vet Sci . (2015) 16: 157–64. doi: 10. 4142/jvs. 2015. 16. 2. 157

10. Darwish AM, Farmer BD, Hawke JP. Improved method for determining antibiotic susceptibility of Flavobacterium columnare isolates by broth microdilution. J Aquat Anim Health . (2008) 20: 185–91. doi: 10. 1577/H07-047. 1

11. Hsu H-M, Bowser PR, Schachte Jr. JH, Scarlett JM, Babish JG. Winter field trials of enrofloxacin for the control of Aeromonas salmonicida infection in salmonids. J World Aquac Soc . (1995) 26: 307–14. doi: 10. 1111/j. 1749-7345. 1995. tb00259. x

12. Hsu H-M, Wooster GA, Bowser PR. Efficacy of enrofloxacin for the treatment of salmonids with bacterial kidney disease, caused by Renibacterium salmoninarum . J Aquat Anim Health . (1994) 6: 220–3. doi: 10. 1577/1548-8667(1994)006 <0220: eoeftt> 2. 3. CO; 2

13. Kyuchukova R, Milanova A, Pavlov A, Lashev L. Comparison of plasma and tissue disposition of enrofloxacin in rainbow trout ( Oncorhynchus mykiss ) and common carp ( Cyprinus carpio ) after a single oral administration. Food Addit Contam Part A Chem Anal Control Expo Risk Assess . (2015) 32: 35–9. doi: 10. 1080/19440049. 2014. 983998

14. Koc F, Uney K, Atamanalp M, Tumer I, Kaban G. Pharmacokinetic disposition of enrofloxacin in brown trout ( Salmo trutta fario ) after oral and intravenous administrations. Aquaculture . (2009) 295: 142–4. doi: 10. 1016/j. aquaculture. 2009. 06. 004

15. Commission of Chinese Veterinary Pharmacopoeia. Enrofloxacin powder (for aquaculture application). (2020). Available online at: http://124. 126. 15. 169: 8081/cx/# (accessed September 10, 2020).

16. Okocha RC, Olatoye IO, Adedeji OB. Food safety impacts of antimicrobial use and their residues in aquaculture. Public Health Reviews . (2018) 39: 21. doi: 10. 1186/s40985-018-0099-2

17. Mo WY, Chen Z, Leung HM, Leung AOW. Application of veterinary antibiotics in China’s aquaculture industry and their potential human health risks. Environ Sci Pollut Res Int . (2017) 24: 8978–89. doi: 10. 1007/s11356-015-5607-z

18. European Union (EU). Directive 2004/28/EC of the European Parliament and of the Council of 31 March 2004 amending Directive 2001/82/EC on the Community code relating to veterinary medicinal products (Text with EEA relevance). (2004). Available online at: https://eur-lex. europa. eu/legal-content/EN/TXT/? uri= celex%3A32004L0028 (accessed September 10, 2020).

PubMed Abstract

19. Yang F, Yang F, Wang G, Kong T, Wang H, Zhang C. Effects of water temperature on tissue depletion of florfenicol and its metabolite florfenicol amine in crucian carp ( Carassius auratus gibelio ) following multiple oral doses. Aquaculture . (2020) 515: 734542. doi: 10. 1016/j. aquaculture. 2019. 734542

20. Barani A, Fallah AA. HPLC analysis of some allowable-antibiotic multiresidues in farmed rainbow trout in Iran. Toxin Rev . (2015) 34: 206–9. doi: 10. 3109/15569543. 2015. 1116097

21. Yang F, Huang XH, Li GH, Ni HJ, Zhao YD, Ding HZ, et al. Estimating tulathromycin withdrawal time in pigs using a physiologically based pharmacokinetics model. Food Addit Contam Part A Chem Anal Control Expo Risk Assess . (2013) 30: 1255–63. doi: 10. 1080/19440049. 2013. 797113

22. Yang F, Si HB, Wang YQ, Zhao ZS, Zhou BH, Hao XQ. Pharmacokinetics of doxycycline in laying hens after intravenous and oral administration. Br Poult Sci . (2016) 57: 576–80. doi: 10. 1080/00071668. 2016. 1184228

23. European Medicines Agency (EMA). Enrofloxacin: Summary report (1)—Committee for Veterinary Medicinal Products . (1996). Available onlineat: https://www. ema. europa. eu/en/documents/mrl-report/enrofloxacin-summary-report-1-committee-veterinary-medicinal-products_en. pdf (accessed September 10, 2020).

PubMed Abstract

24. Yang F, Sun N, Sun YX, Shan Q, Zhao HY, Zeng DP, et al. A physiologically based pharmacokinetics model for florfenicol in crucian carp and oral-to-intramuscular extrapolation. J Vet Pharmacol Ther . (2013) 36: 192–200. doi: 10. 1111/j. 1365-2885. 2012. 01419. x

25. Xu N, Li M, Chou WC, Lin Z. A physiologically based pharmacokinetic model of doxycycline for predicting tissue residues and withdrawal intervals in grass carp ( Ctenopharyngodon idella ). Food Chem Toxicol . (2020) 137: 111127. doi: 10. 1016/j. fct. 2020. 111127

26. Yang F, Yang F, Shi W, Si H, Kong T, Wang G, et al. Development of a multiroute physiologically based pharmacokinetic model for orbifloxacin in rabbits. J Vet Pharmacol Ther . (2018) 41: 622–31. doi: 10. 1111/jvp. 12496

27. Leavens TL, Tell LA, Kissell LW, Smith GW, Smith DJ, Wagner SA, et al. Development of a physiologically based pharmacokinetic model for flunixin in cattle ( Bos taurus ). Food Addit Contam Part A Chem Anal Control Expo Risk Assess . (2014) 31: 1506–21. doi: 10. 1080/19440049. 2014. 938363

28. Yang F, Sun N, Liu YM, Zeng ZL. Estimating danofloxacin withdrawal time in broiler chickens based on physiologically based pharmacokinetics modeling. J Vet Pharmacol Ther . (2015) 38: 174–82. doi: 10. 1111/jvp. 12162

29. Yang F, Yang YR, Wang L, Huang XH, Qiao G, Zeng ZL. Estimating marbofloxacin withdrawal time in broiler chickens using a population physiologically based pharmacokinetics model. J Vet Pharmacol Ther . (2014) 37: 579–88. doi: 10. 1111/jvp. 12137

30. Li M, Gehring R, Riviere JE, Lin Z. Development and application of a population physiologically based pharmacokinetic model for penicillin G in swine and cattle for food safety assessment. Food Chem Toxicol . (2017) 107: 74–87. doi: 10. 1016/j. fct. 2017. 06. 023

31. Li M, Gehring R, Riviere JE, Lin Z. Probabilistic physiologically based pharmacokinetic model for penicillin G in milk from dairy cows following intramammary or intramuscular administrations. Toxicol Sci . (2018) 164: 85–100. doi: 10. 1093/toxsci/kfy067

32. Lin Z, Gehring R, Mochel JP, Lave T, Riviere JE. Mathematical modeling and simulation in animal health—Part II: principles, methods, applications, and value of physiologically based pharmacokinetic modeling in veterinary medicine and food safety assessment. J Vet Pharmacol Ther . (2016) 39: 421–38. doi: 10. 1111/jvp. 12311

33. Abbas R, Hayton WL. A physiologically based pharmacokinetic and pharmacodynamic model for paraoxon in rainbow trout. Toxicol Appl Pharmacol . (1997) 145: 192–201. doi: 10. 1006/taap. 1997. 8168

34. Erickson RJ, McKim JM. A simple flow-limited model for exchange of organic chemicals at fish gills. Environ Toxicol Chem . (1990) 9: 159–65. doi: 10. 1002/etc. 5620090205

35. Nichols JW, McKim JM, Andersen ME, Gargas ML, Clewell HJ, Erickson RJ. A physiologically based toxicokinetic model for the uptake and disposition of waterborne organic chemicals in fish. Toxicol Appl Pharmacol . (1990) 106: 433–47. doi: 10. 1016/0041-008x(90)90338-u

36. Salmina ES, Wondrousch D, Kuhne R, Potemkin VA, Schuurmann G. Variation in predicted internal concentrations in relation to PBPK model complexity for rainbow trout. Sci Total Environ . (2016) 550: 586–97. doi: 10. 1016/j. scitotenv. 2016. 01. 107

37. Bowser PR, Wooster GA, St Leger J, Babish JG. Pharmacokinetics of enrofloxacin in fingerling rainbow trout ( Oncorhynchus mykiss ). J Vet Pharmacol Ther . (1992) 15: 62–71. doi: 10. 1111/j. 1365-2885. 1992. tb00987. x

38. Urzua N, Messina MJ, Prieto G, Luders C, Errecalde C. Pharmacokinetics and tissue disposition of enrofloxacin in rainbow trout after different routes of administration. Xenobiotica . (2020) 50: 1236–41. doi: 10. 1080/00498254. 2020. 1747119

39. Pan H. Effect of water velocity, temperature and light intensity on pharmacokinetics of enrofloxacin in rainbow (dissertation/master’s thesis). Shanghai Ocean University, Shanghai (2017).

40. Sadiq MW, Nielsen EI, Khachman D, Conil JM, Georges B, Houin G, et al. A whole-body physiologically based pharmacokinetic (WB-PBPK) model of ciprofloxacin: a step towards predicting bacterial killing at sites of infection. J Pharmacokinet Pharmacodyn . (2017) 44: 69–79. doi: 10. 1007/s10928-016-9486-9

41. Yang F, Lin Z, Riviere JE, Baynes RE. Development and application of a population physiologically based pharmacokinetic model for florfenicol and its metabolite florfenicol amine in cattle. Food Chem Toxicol . (2019) 126: 285–94. doi: 10. 1016/j. fct. 2019. 02. 029

42. Barron MG, Tarr BD, Hayton WL. Temperature-dependence of cardiac output and regional blood flow in rainbow trout, Salmo gairdneri Richardson. J Fish Biol . (1987) 31: 735–44. doi: 10. 1111/j. 1095-8649. 1987. tb05276. x

43. Gallo JM, Lam FC, Perrier DG. Area method for the estimation of partition coefficients for physiological pharmacokinetic models. J Pharmacokinet Biopharm . (1987) 15: 271–80. doi: 10. 1007/BF01066322

44. Steffenak I, Hormazabal V, Yndestad M. Reservoir of quinolone residues in fish. Food Addit Contam . (1991) 8: 777–80. doi: 10. 1080/02652039109374035