# Aerobic Biodegradation of Four Groups of Steroid Hormones in Activated Sludge

Authors: Jiaxin Zhang; Jun Luo; Hong Chang
Journal: Journal of Chemistry
 (2020)

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## Abstract

Steroid hormones in the environment have obtained considerable attention, as they can be harmful to aquatic organisms at very low concentrations. An analytical method was developed for simultaneously monitoring four estrogens, seven androgens, seven progestogens, and eleven glucocorticoids in a single water sample using liquid chromatography-electrospray tandem mass spectrometry. Laboratory studies were then performed to investigate the aerobic biodegradation of 29 steroids belonging to the four groups. The degradation of target steroids followed first-order reaction kinetics, and the degradation half-life (t1/2) of estrogens, androgens, progestogens and glucocorticoids was 1.2–8.7 h, 0.3–1.3 h, 1.4–7.7 h, and 1.4–23.1 h, respectively. Most of the esterified glucocorticoids were more persistent than the parent compounds, but the t1/2 for halogenated glucocorticoids was longer than that of their esterified compounds. In addition, C-21 ester glucocorticoids were more prone to decomposition than C-17 esters. Hydrolysis did not significantly affect the decomposition of esterified steroids.


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## Body

## 1. Introduction

The presence of endocrine-disrupting chemicals (EDCs) in the environment is of wide concern throughout the world. Among EDCs, steroidal estrogens have obtained considerable attention, as they can be harmful to aquatic organisms, such as fish and amphibians, at very low concentrations [1, 2]. In addition to estrogens, other steroid hormones such as androgens, progestogens, and glucocorticoids have recently been documented to present a risk to exposed organisms [3–5]. Therefore, the occurrence and fate of steroid hormones other than estrogens in the environment deserve greater attention.The presence of the four groups of steroid hormones and, in particular, estrogens in surface waters has been reported in multiple studies, and their concentrations were in the range of pg/L to several hundreds of ng/L [6–11]. Wastewater treatment plants (WWTPs) such as municipal and livestock WWTPs play a crucial role in restricting steroid hormones from entering riverine and coastal environments [12, 13]. Incomplete removal of these steroids in WWTPs could result in the contamination of surface waters. Thus, it is essential to study the biodegradation of steroids by bacteria in activated sludge, particularly that of progestogens and glucocorticoids.Microbial processes play an essential role in steroid degradation. Such processes have been particularly well documented for the microbiological degradation of estrogens and androgens [14–19]. However, for progestogens and glucocorticoids, most studies have been mainly concerned about their concentrations in WWTP influents and effluents and receiving waters. To our knowledge, few studies reported the degradation kinetics of progestogens [8, 20] and glucocorticoids [21] by aerobic sludge. Miyamoto et al. [21] studied the fate of 10 glucocorticoids upon incubation with activated sludge and revealed different degradation behaviours for structurally different glucocorticoids. However, no studies have simultaneously investigated the microbial degradation of the four groups of steroids.This study was performed to assess the degradation of four groups of steroids, including estrogens, androgens, progestogens, and glucocorticoids, upon treatment with activated sludge. A sensitive and reliable ultrahigh-performance liquid chromatography-tandem mass spectrometry (UPLC-MS/MS) method combined with liquid-liquid extraction (LLE) was developed for the simultaneous analysis of the four groups of steroids (including four estrogens, seven androgens, seven progestogens, and eleven glucocorticoids; see Table1) in water samples. Due to the presence of isomers of the target steroids, effective chromatographic separation is essential for the unequivocal identification of specific compounds. Activated sludge was obtained from a working WWTP in Beijing, China. We simultaneously analyzed the degradation kinetics of 29 steroids during aerobic incubation with activated sludge and compared the rate of degradation among the four groups. This study will help understand their removal behaviour in the environment and consequently help accurately assess the risk of steroids hormones [22, 23].Table 1
Optimized instrumental and MRM conditions of the target compounds.
Analyte
Abbreviation
Mode
Precursor ion
MRM transition
CV (V)
CE (eV)
IDL (μg/L)
Estrogens
Estrone
E1
ESI+
[M-OH]+
271 > 147a
18
10
2.0
271 > 197b
17
α-Estradiol
αE2
ESI+
[M-OH]+
255 > 159
35
20
0.20
255 > 133
20
β-Estradiol
βE2
ESI+
[M-OH]+
255 > 159
35
20
1.0
255 > 133
20
Ethinylestradiol
EE2
ESI+
[M-OH]+
279 > 133
24
16
1.0
279 > 159
21
Androgens
Testosterone
T
ESI+
[M + H]+
289 > 97
35
20
2.0
289 > 109
20
Methyl-testosterone
MT
ESI+
[M + H]+
303 > 97
22
22
1.8
303 > 109
15
epitestosterone
ET
ESI+
[M + H]+
289 > 97
35
20
1.5
289 > 109
20
Trenbolone
TBL
ESI+
[M + H]+
271 > 253
22
18
1.5
271 > 199
22
Boldenone
BOL
ESI+
[M + H]+
287 > 121
24
22
3.3
287 > 135
15
Dehydroepiandrosterone
DEHA
ESI+
[M + H]+
271 > 253
28
24
2.4
271 > 199
cis-Androsterone
cis-ADR
ESI+
[M + H]+
273 > 255
20
15
5.0
273 > 273
10
Progestogens
Progesterone
P
ESI+
[M + H]+
351 > 109
35
20
1.3
351 > 97
16
21α-Hydroxyprogesterone
21α-HPT
ESI+
[M + H]+
331 > 108
28
22
1.0
331 > 97
21
17α-Hydroxyprogesterone
17α-HPT
ESI+
[M + H]+
331 > 108
28
22
1.0
331 > 97
21
19-Nortestosterone
19-NT
ESI+
[M + H]+
275 > 257
28
15
0.15
275 > 239
15
Medroxyprogesterone acetate
MPA
ESI+
[M + H]+
387 > 327
28
16
0.20
387 > 285
16
19-Norethindrone
19-NTD
ESI+
[M + H]+
299 > 231
24
17
3.0
299 > 109
24
Melengestrol acetate
MGA
ESI+
[M + H]+
397 > 337
26
15
0.05
397 > 279
20
Glucocorticoids
Cortisol
CRL
ESI-
[M-CH2COO]−
421 > 331
30
16
0.40
421 > 361
16
Cortisol 17 acetate
17-CRLA
ESI-
[M-CH2COO]−
463 > 403
27
11
0.17
463 > 373
16
Cortisol 21 acetate
21-CRLA
ESI-
[M-CH2COO]−
463 > 403
27
11
0.26
463 > 373
16
Cortisol 17-valerate
17-CRLV
ESI-
[M-CH2COO]−
505 > 455
20
10
0.12
505 > 331
16
Cortisol 21-valerate
21-CRLV
ESI-
[M-CH2COO]−
505 > 455
20
10
0.18
505 > 331
16
Betamethasone
BET
ESI-
[M-CH2COO]−
451 > 361
27
16
0.44
451 > 391
11
Dexamethasone
DEX
ESI-
[M-CH2COO]−
451 > 361
27
16
0.85
451 > 391
11
Betamethasone acetate
BETA
ESI-
[M-CH2COO]−
493 > 433
20
12
0.33
493 > 353
18
Dexamethasone acetate
DEXA
ESI-
[M-CH2COO]−
493 > 433
20
12
0.48
493 > 353
18
Cortisone
COR
ESI-
[M-CH2COO]−
419 > 331
30
16
0.60
419 > 361
16
Cortisone acetate
CORA
ESI-
[M-CH2COO]−
461 > 371
27
25
0.14
461 > 401
16
For all the compounds,a is the first MRM transition used for quantification, and b is the second MRM transition used for verification.


## 2. Materials and Methods

### 2.1. Chemicals and Sludge Collection

Twenty-nine steroids were purchased from Sigma (St. Louis, MO, USA). Methanol, ethyl acetate, acetonitrile, acetic acid, hexane, and methylene chloride were of HPLC grade and obtained from Fisher Chemicals (Beijing, China). The activated sludge that was used as the inoculum was collected from the aerobic tank of one WWTP in Beijing, China. The slurry samples were transported back to the laboratory, stored at 4°C, and used within 24 h.


### 2.2. Microcosms

Aerobic microcosms were prepared by using fresh activated (aerobic) sludge. Incubation solutions containing 5% of each inoculum (v/v) were cultivated in a minimal-salt medium consisting of KH2PO4 (85 mg/L), NH4Cl (5 mg/L), MgSO4·7H2O (22.5 mg/L), FeCl3·6H2O (0.25 mg/L), NaHPO4·2H2O (334 mg/L), CaCl2·2H2O (36.4 mg/L), K2HPO4 (217.5 mg/L), vitamins, and trace salts, including biotin (40 mg/L), folic acid (40 mg/L), riboflavin (100 mg/L), pantothenic acid (100 mg/L), para-aminobenzoic acid (100 mg/L), niacin (100 mg/L), thiamine (100 mg/L), vitamin B6 (200 mg/L), and vitamin B12 (2 mg/L). The pH of the medium was adjusted to 7.0.


### 2.3. Degradation Experiments

The degradation experiments were performed in two groups, including groups A (test replicates) and B (sterile controls). Each group was evaluated in three 100 mL glass conical flasks with 25 mL of media containing 1.25 mL of activated sludge. The studied compounds were spiked into the incubation media of each treatment by adding 12.5μL of each steroid stock solution (1000 mg/L). This rendered an initial concentration of each studied compounds in each treatment of 500 μg/L.Three replicates (A1, A2, and A3) were used to monitor the degradation of each steroid at predetermined sampling time intervals (0, 0.5, 1.0, 1.5, 2.0, 3.0, 5.0, 7.0, 10.0, 12.0, 24.0, 36.0, 48.0, and 60.0 h). At each sampling time point, 1 mL of solution was removed from the same glass conical flask and transferred into a 2 mL amber glass vial to extract the remaining compounds of interest. For the sterile controls of each treatment (B1, B2, and B3), the glass conical flasks containing incubation media were autoclaved (120°C, 30 min) three times in three consecutive days prior to experimentation, followed by the addition of 0.1 mL of HgCl2 (100 mg/L) to maintain sterility. The target steroids were then added to each sterile control. Sterile controls for each treatment were then sampled at the same sampling points as the test groups (group A).The treated flasks were covered with sterile sealing membranes to prevent bacteria from entering, while allowing air to circulate. The six flasks were incubated in the dark at 28°C with continuous shaking at 150 rpm to maintain aerobic conditions before sampling.


### 2.4. Sample Pretreatment and UPLC-MS/MS Analysis

Samples (1 mL) were collected from the incubation media (A1–A3 and B1–B3) and extracted by 1 mL of ethyl acetate three times. The mixture was thoroughly mixed before each extraction using a Vortex mixer. The extracts were dried with weak nitrogen and redissolved in 200μL of methanol for analysis.The LC apparatus was an ACQUITY Ultra Performance LC system (Waters, Milford, MA, USA). Separation was conducted using a Waters HSS T3 column (100 mm × 2.1 mm, 1.8μm, Waters, USA). The column was maintained at 40°C, and the flow rate and injection volume were 0.2 mL/min and 5 μL, respectively. The mobile phases consisted of acetonitrile containing acetic acid (0.15%, v/v) as solvent A and Milli-Q water containing acetic acid (0.15%, v/v) as solvent B. The initial gradient elution of 15% A was held for 9 min and then increased to 35% A in 4 min and 85% A in 5 min. Following the gradient elution, a final elution with 15% A was held for 4 min.Mass spectrometry was performed using a Waters Premier XE Mass Spectrometer equipped with an electrospray ionization source (Waters). A flow injection of a standard solution of each compound was used to determine the optimum conditions for the ESI source. The average parameters were source temperature, 100°C; desolvation temperature, 350°C; capillary voltage, 3.2 kV; desolvation gas flow rate, 800 L/h; and cone gas flow rate, 50 L/h. Quantitative analyses of the target glucocorticoids were performed in the multiselected reaction monitoring (MRM) mode. Data acquisition was performed with MassLynx 4.1 (Micromass, Manchester, U. K.).


## 2.1. Chemicals and Sludge Collection

Twenty-nine steroids were purchased from Sigma (St. Louis, MO, USA). Methanol, ethyl acetate, acetonitrile, acetic acid, hexane, and methylene chloride were of HPLC grade and obtained from Fisher Chemicals (Beijing, China). The activated sludge that was used as the inoculum was collected from the aerobic tank of one WWTP in Beijing, China. The slurry samples were transported back to the laboratory, stored at 4°C, and used within 24 h.


## 2.2. Microcosms

Aerobic microcosms were prepared by using fresh activated (aerobic) sludge. Incubation solutions containing 5% of each inoculum (v/v) were cultivated in a minimal-salt medium consisting of KH2PO4 (85 mg/L), NH4Cl (5 mg/L), MgSO4·7H2O (22.5 mg/L), FeCl3·6H2O (0.25 mg/L), NaHPO4·2H2O (334 mg/L), CaCl2·2H2O (36.4 mg/L), K2HPO4 (217.5 mg/L), vitamins, and trace salts, including biotin (40 mg/L), folic acid (40 mg/L), riboflavin (100 mg/L), pantothenic acid (100 mg/L), para-aminobenzoic acid (100 mg/L), niacin (100 mg/L), thiamine (100 mg/L), vitamin B6 (200 mg/L), and vitamin B12 (2 mg/L). The pH of the medium was adjusted to 7.0.


## 2.3. Degradation Experiments

The degradation experiments were performed in two groups, including groups A (test replicates) and B (sterile controls). Each group was evaluated in three 100 mL glass conical flasks with 25 mL of media containing 1.25 mL of activated sludge. The studied compounds were spiked into the incubation media of each treatment by adding 12.5μL of each steroid stock solution (1000 mg/L). This rendered an initial concentration of each studied compounds in each treatment of 500 μg/L.Three replicates (A1, A2, and A3) were used to monitor the degradation of each steroid at predetermined sampling time intervals (0, 0.5, 1.0, 1.5, 2.0, 3.0, 5.0, 7.0, 10.0, 12.0, 24.0, 36.0, 48.0, and 60.0 h). At each sampling time point, 1 mL of solution was removed from the same glass conical flask and transferred into a 2 mL amber glass vial to extract the remaining compounds of interest. For the sterile controls of each treatment (B1, B2, and B3), the glass conical flasks containing incubation media were autoclaved (120°C, 30 min) three times in three consecutive days prior to experimentation, followed by the addition of 0.1 mL of HgCl2 (100 mg/L) to maintain sterility. The target steroids were then added to each sterile control. Sterile controls for each treatment were then sampled at the same sampling points as the test groups (group A).The treated flasks were covered with sterile sealing membranes to prevent bacteria from entering, while allowing air to circulate. The six flasks were incubated in the dark at 28°C with continuous shaking at 150 rpm to maintain aerobic conditions before sampling.


## 2.4. Sample Pretreatment and UPLC-MS/MS Analysis

Samples (1 mL) were collected from the incubation media (A1–A3 and B1–B3) and extracted by 1 mL of ethyl acetate three times. The mixture was thoroughly mixed before each extraction using a Vortex mixer. The extracts were dried with weak nitrogen and redissolved in 200μL of methanol for analysis.The LC apparatus was an ACQUITY Ultra Performance LC system (Waters, Milford, MA, USA). Separation was conducted using a Waters HSS T3 column (100 mm × 2.1 mm, 1.8μm, Waters, USA). The column was maintained at 40°C, and the flow rate and injection volume were 0.2 mL/min and 5 μL, respectively. The mobile phases consisted of acetonitrile containing acetic acid (0.15%, v/v) as solvent A and Milli-Q water containing acetic acid (0.15%, v/v) as solvent B. The initial gradient elution of 15% A was held for 9 min and then increased to 35% A in 4 min and 85% A in 5 min. Following the gradient elution, a final elution with 15% A was held for 4 min.Mass spectrometry was performed using a Waters Premier XE Mass Spectrometer equipped with an electrospray ionization source (Waters). A flow injection of a standard solution of each compound was used to determine the optimum conditions for the ESI source. The average parameters were source temperature, 100°C; desolvation temperature, 350°C; capillary voltage, 3.2 kV; desolvation gas flow rate, 800 L/h; and cone gas flow rate, 50 L/h. Quantitative analyses of the target glucocorticoids were performed in the multiselected reaction monitoring (MRM) mode. Data acquisition was performed with MassLynx 4.1 (Micromass, Manchester, U. K.).


## 3. Results and Discussion

### 3.1. Method Development

The 29 steroids, including four estrogens, seven androgens, seven progestogens, and eleven glucocorticoids, were simultaneously analyzed by MS/MS in the MRM mode. The two abundant MRM transitions, cone voltage and collision energies, were optimized for each analyte by infusing the standard solutions into the mass spectrometer (see Table1). The ESI-MS/MS analyses of glucocorticoids were operated in the negative mode, while estrogen, androgen, and progestogen were operated in the positive ion mode. The precursor ions for estrogens and glucocorticoids were [M-OH]+ and [M-CH2COO]−, respectively, while the precursor ions for androgens and progestogens were protonated molecular ions ([M + H]+).Chromatographic separation is important for the clear identification of the 29 target steroids because some of the target compounds were isomers with identical precursor and product ions. In this study, the use of C18 column chemistry failed to effectively separate some isomers. Thus, we also evaluated HSS T3 columns, which afforded better separation and retention of all of the target compounds. The LODs were estimated based on the peak-to-peak noise of the baseline near the peak of the analyte. The LODs were determined as the concentration with a minimum S/N ratio of 3. Figure1 shows the UPLC-MS-MS chromatogram of the 29 steroids in less than 20 min. Very low instrumental detection limits (IDLs) were obtained for the 29 analytes (0.15–0.85 μg/L) (see Table 1).Figure 1
UPLC-MS/MS MRM chromatograms of target steroids.LLE was used to extract the target steroids in the degradation experiment. Three organic solvents were evaluated, including ethyl acetate, n-hexane, and dichloromethane. As shown in Figure2, ethyl acetate had high recoveries of estrogens, androgens, progestogens, and glucocorticoids of 87–90%, 61–100%, 96–100%, and 58–100%, respectively. In contrast, the low polar solvents, n-hexane and dichloromethane, produced very low recoveries (1–30%) for glucocorticoids, which was expected as glucocorticoids are polar compounds with log Kow of approximately 1. For estrogens, the three solvents produced similar recoveries. For androgens and progestogens, the recoveries of n-hexane and dichloromethane were 38–57%. Thus, ethyl acetate was selected as the extraction solvent for all four classes of steroids in this study.Figure 2
Recoveries (%) of target steroids with different elution solvents.


### 3.2. Kinetics of Steroid Biodegradation

We investigated the degradation of steroids in laboratory-scale experiments, and the degradation profiles of the 29 target compounds are shown in Figure3. The residual steroid concentrations at 0 h are expressed as 100%. No significant losses of the target compounds were observed in the sterile control reactions. Thus, we know that the reductions of the 29 steroids in the test groups (group A) were due to biological degradation, while the contribution from abiotic degradation, such as adsorption was very small.Figure 3
Degradation curves of steroids with 5% sludge concentrations. NS (nonsterile): slurry + steroids and S (sterile): slurry + steroids + HgCl2.
(a)
(b)For the steroids studied, aerobic biodegradation followed first-order reaction kinetics. The kinetic parameters, including half-life (t1/2) and kinetic rate constant (k), are summarized in Table 2. The degradation t1/2 of estrogens, androgens, progestogens, and glucocorticoids were 1.2–8.7 h, 0.3–1.3 h, 1.4–7.7 h, and 1.4–23.1 h, respectively, indicating that the degradation of androgens was the fastest, followed by estrogens, progestogens, and glucocorticoids under the same experimental conditions. Thus, compounds were all nearly fully degraded after 30 h of digestion.Table 2
Degradation parameters of the first-order kinetics model.
Analyte
First-order kinetics
k
1 (h−1)
t
1/2 (h)
r
2
Estrogens
E1
0.16
4.3
0.9407
αE2
0.26
2.7
0.9268
βE2
0.59
1.2
0.8909
EE2
0.08
8.7
0.9526
Androgens
T
1.51
0.5
0.9466
MT
0.57
1.2
0.9817
ET
2.02
0.3
0.9762
TBL
1.35
0.5
0.9773
BLE
1.56
0.4
0.9801
DEHA
0.67
1.0
0.9710
C-ADR
0.75
0.9
0.8941
Progestogens
P
0.28
2.5
0.9002
21α-HPT
0.26
2.7
0.8907
17α-HPT
0.30
2.3
0.8936
19-NT
0.49
1.4
0.9726
MPA
0.19
3.6
0.8935
19-NTD
0.28
2.5
0.9077
MGA
0.09
7.7
0.9930
Glucocorticoids
CRL
0.28
2.5
0.9712
17-CRLA
0.12
5.8
0.9454
21-CRLA
0.15
4.6
0.9199
17-CRLV
0.10
6.9
0.9587
21-CRLV
0.20
3.5
0.9120
BET
0.03
23.1
0.9770
DEX
0.04
17.3
0.9876
BETA
0.35
2.0
0.9262
DEXA
0.28
2.5
0.8992
COR
0.48
1.4
0.9521
CORA
0.32
2.2
0.9829The androgens were all natural hormones, which is likely why their decomposition rates were the fastest. According to the degradation curves of androgens, almost all of which were decomposed within 3 h of digestion. In addition, thet1/2 of androgens (0.3–1.3 h) was consistent with that reported by Chang et al. [8]. Estrogens including E1, αE2, βE2, and EE2 were almost decomposed within 24 h of digestion. The decomposition rate of synthetic EE2 was much slower than that of the other three natural estrogens, which is also consistent with the results of previous studies [24–27].Compared to natural compounds, synthetic progestogens such as MPA and MGA were also not readily degraded. The decomposition rates of glucocorticoids ranged from 1.4 h (COR) to 23.1 h (BET). It is interesting to note that most of the esterified glucocorticoids such as 17-CRLA, 21-CRLA, 17-CRLV, and 21-CRLV were more persistent relative to their parent compounds; however, this was not true for halogenated glucocorticoids, such as DEX and BET. Thet1/2 of DEX (17.3 h) and BET (23.1 h) were significantly higher than that of their esterified compounds (DEXA: 2.5 h; BETA: 2.0 h). These results may be because the decomposition of halogenated glucocorticoids is more difficult than the hydrolysis of their esterified compounds. In addition, it was found that C-21 esters (21-CRLA and 21-CRLV) were prone to decomposition compared to C-17 esters (17-CRLA and 21-CRLV). Those findings are different from the recovery results reported by our recent study [11]. That study found C-17 esters were prone to hydrolysis in pure water, even under neutral conditions. Thus, hydrolysis did not significantly affect the decomposition of esterified steroids in this study.The first-order kinetics model was applied to fit the degradation results. C0 is initial concentration of steroids (500 μg/L); Ct is the concentrations of compounds at time t; and k1 is the first-order rate constant. t1/2 can be calculated as 0.693/k1.


## 3.1. Method Development

The 29 steroids, including four estrogens, seven androgens, seven progestogens, and eleven glucocorticoids, were simultaneously analyzed by MS/MS in the MRM mode. The two abundant MRM transitions, cone voltage and collision energies, were optimized for each analyte by infusing the standard solutions into the mass spectrometer (see Table1). The ESI-MS/MS analyses of glucocorticoids were operated in the negative mode, while estrogen, androgen, and progestogen were operated in the positive ion mode. The precursor ions for estrogens and glucocorticoids were [M-OH]+ and [M-CH2COO]−, respectively, while the precursor ions for androgens and progestogens were protonated molecular ions ([M + H]+).Chromatographic separation is important for the clear identification of the 29 target steroids because some of the target compounds were isomers with identical precursor and product ions. In this study, the use of C18 column chemistry failed to effectively separate some isomers. Thus, we also evaluated HSS T3 columns, which afforded better separation and retention of all of the target compounds. The LODs were estimated based on the peak-to-peak noise of the baseline near the peak of the analyte. The LODs were determined as the concentration with a minimum S/N ratio of 3. Figure1 shows the UPLC-MS-MS chromatogram of the 29 steroids in less than 20 min. Very low instrumental detection limits (IDLs) were obtained for the 29 analytes (0.15–0.85 μg/L) (see Table 1).Figure 1
UPLC-MS/MS MRM chromatograms of target steroids.LLE was used to extract the target steroids in the degradation experiment. Three organic solvents were evaluated, including ethyl acetate, n-hexane, and dichloromethane. As shown in Figure2, ethyl acetate had high recoveries of estrogens, androgens, progestogens, and glucocorticoids of 87–90%, 61–100%, 96–100%, and 58–100%, respectively. In contrast, the low polar solvents, n-hexane and dichloromethane, produced very low recoveries (1–30%) for glucocorticoids, which was expected as glucocorticoids are polar compounds with log Kow of approximately 1. For estrogens, the three solvents produced similar recoveries. For androgens and progestogens, the recoveries of n-hexane and dichloromethane were 38–57%. Thus, ethyl acetate was selected as the extraction solvent for all four classes of steroids in this study.Figure 2
Recoveries (%) of target steroids with different elution solvents.


## 3.2. Kinetics of Steroid Biodegradation

We investigated the degradation of steroids in laboratory-scale experiments, and the degradation profiles of the 29 target compounds are shown in Figure3. The residual steroid concentrations at 0 h are expressed as 100%. No significant losses of the target compounds were observed in the sterile control reactions. Thus, we know that the reductions of the 29 steroids in the test groups (group A) were due to biological degradation, while the contribution from abiotic degradation, such as adsorption was very small.Figure 3
Degradation curves of steroids with 5% sludge concentrations. NS (nonsterile): slurry + steroids and S (sterile): slurry + steroids + HgCl2.
(a)
(b)For the steroids studied, aerobic biodegradation followed first-order reaction kinetics. The kinetic parameters, including half-life (t1/2) and kinetic rate constant (k), are summarized in Table 2. The degradation t1/2 of estrogens, androgens, progestogens, and glucocorticoids were 1.2–8.7 h, 0.3–1.3 h, 1.4–7.7 h, and 1.4–23.1 h, respectively, indicating that the degradation of androgens was the fastest, followed by estrogens, progestogens, and glucocorticoids under the same experimental conditions. Thus, compounds were all nearly fully degraded after 30 h of digestion.Table 2
Degradation parameters of the first-order kinetics model.
Analyte
First-order kinetics
k
1 (h−1)
t
1/2 (h)
r
2
Estrogens
E1
0.16
4.3
0.9407
αE2
0.26
2.7
0.9268
βE2
0.59
1.2
0.8909
EE2
0.08
8.7
0.9526
Androgens
T
1.51
0.5
0.9466
MT
0.57
1.2
0.9817
ET
2.02
0.3
0.9762
TBL
1.35
0.5
0.9773
BLE
1.56
0.4
0.9801
DEHA
0.67
1.0
0.9710
C-ADR
0.75
0.9
0.8941
Progestogens
P
0.28
2.5
0.9002
21α-HPT
0.26
2.7
0.8907
17α-HPT
0.30
2.3
0.8936
19-NT
0.49
1.4
0.9726
MPA
0.19
3.6
0.8935
19-NTD
0.28
2.5
0.9077
MGA
0.09
7.7
0.9930
Glucocorticoids
CRL
0.28
2.5
0.9712
17-CRLA
0.12
5.8
0.9454
21-CRLA
0.15
4.6
0.9199
17-CRLV
0.10
6.9
0.9587
21-CRLV
0.20
3.5
0.9120
BET
0.03
23.1
0.9770
DEX
0.04
17.3
0.9876
BETA
0.35
2.0
0.9262
DEXA
0.28
2.5
0.8992
COR
0.48
1.4
0.9521
CORA
0.32
2.2
0.9829The androgens were all natural hormones, which is likely why their decomposition rates were the fastest. According to the degradation curves of androgens, almost all of which were decomposed within 3 h of digestion. In addition, thet1/2 of androgens (0.3–1.3 h) was consistent with that reported by Chang et al. [8]. Estrogens including E1, αE2, βE2, and EE2 were almost decomposed within 24 h of digestion. The decomposition rate of synthetic EE2 was much slower than that of the other three natural estrogens, which is also consistent with the results of previous studies [24–27].Compared to natural compounds, synthetic progestogens such as MPA and MGA were also not readily degraded. The decomposition rates of glucocorticoids ranged from 1.4 h (COR) to 23.1 h (BET). It is interesting to note that most of the esterified glucocorticoids such as 17-CRLA, 21-CRLA, 17-CRLV, and 21-CRLV were more persistent relative to their parent compounds; however, this was not true for halogenated glucocorticoids, such as DEX and BET. Thet1/2 of DEX (17.3 h) and BET (23.1 h) were significantly higher than that of their esterified compounds (DEXA: 2.5 h; BETA: 2.0 h). These results may be because the decomposition of halogenated glucocorticoids is more difficult than the hydrolysis of their esterified compounds. In addition, it was found that C-21 esters (21-CRLA and 21-CRLV) were prone to decomposition compared to C-17 esters (17-CRLA and 21-CRLV). Those findings are different from the recovery results reported by our recent study [11]. That study found C-17 esters were prone to hydrolysis in pure water, even under neutral conditions. Thus, hydrolysis did not significantly affect the decomposition of esterified steroids in this study.The first-order kinetics model was applied to fit the degradation results. C0 is initial concentration of steroids (500 μg/L); Ct is the concentrations of compounds at time t; and k1 is the first-order rate constant. t1/2 can be calculated as 0.693/k1.


## 4. Conclusions

The UPLC-MS/MS method with a high selectivity and sensitivity was developed for the simultaneous determination of 29 steroids in water samples, including estrogens, androgens, progestogens, and glucocorticoids. The decomposition rate of androgens was the fastest, followed by estrogens and progestogens. The degradation of glucocorticoids was the slowest of the four groups of steroids, with DEX and BET having the longestt1/2 among all such steroids. Hydrolysis did not significantly affect the decomposition of esterified steroids in this study.



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*Source: 1309183-2020-03-09.xml*