energies
Article
Metagenomic Analysis of the Long-Term Synergistic Effects of
Antibiotics on the Anaerobic Digestion of Cattle Manure
Izabela Wolak 1 , Małgorzata Czatzkowska 1 , Monika Harnisz 1 , Jan Paweł Jastrz˛ebski 2 , Łukasz Paukszto 3 ,
Paulina Rusanowska 4 , Ewa Felis 5 and Ewa Korzeniewska 1, *
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2
3
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5
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Citation: Wolak, I.; Czatzkowska, M.;
Harnisz, M.; Jastrz˛ebski, J.P.;
Paukszto, Ł.; Rusanowska, P.; Felis,
E.; Korzeniewska, E. Metagenomic
Analysis of the Long-Term
Synergistic Effects of Antibiotics on
the Anaerobic Digestion of Cattle
Manure. Energies 2022, 15, 1920.
https://doi.org/10.3390/en15051920
Academic Editors: Timo Kikas,
Abrar Inayat and Lisandra
Rocha Meneses
Received: 16 February 2022
Accepted: 4 March 2022
Published: 6 March 2022
Publisher’s Note: MDPI stays neutral
Department of Water Protection Engineering and Environmental Microbiology, Faculty of Geoengineering,
University of Warmia and Mazury in Olsztyn, Prawocheńskiego 1, 10-720 Olsztyn, Poland;
izabela.koniuszewska@uwm.edu.pl (I.W.); malgorzata.czatzkowska@uwm.edu.pl (M.C.);
monika.harnisz@uwm.edu.pl (M.H.)
Department of Physiology, Genetics and Plant Biotechnology, Faculty of Biology and Biotechnology,
University of Warmia and Mazury in Olsztyn, Oczapowskiego 1A, 10-957 Olsztyn, Poland;
jan.jastrzebski@uwm.edu.pl
Department of Botany and Nature Protection, Faculty of Biology and Biotechnology, University of Warmia
and Mazury in Olsztyn, Plac Łódzki 1, 10-721 Olsztyn, Poland; pauk24@gmail.com
Department of Environmental Engineering, University of Warmia and Mazury in Olsztyn, Warszawska 117,
10-950 Olsztyn, Poland; paulina.jaranowska@uwm.edu.pl
Department of Environmental Biotechnology, Faculty of Energy and Environmental Engineering,
Silesian University of Technology, Akademicka 2, 44-100 Gliwice, Poland; ewa.felis@polsl.pl
Correspondence: ewa.korzeniewska@uwm.edu.pl; Tel.: +48-89-523-37-52
Abstract: The conversion of cattle manure into biogas in anaerobic digestion (AD) processes has been
gaining attention in recent years. However, antibiotic consumption continues to increase worldwide,
which is why antimicrobial concentrations can be expected to rise in cattle manure and in digestate.
This study examined the long-term synergistic effects of antimicrobials on the anaerobic digestion
of cattle manure. The prevalence of antibiotic resistance genes (ARGs) and changes in microbial
biodiversity under exposure to the tested drugs was investigated using a metagenomic approach.
Methane production was analyzed in lab-scale anaerobic bioreactors. Bacteroidetes, Firmicutes, and
Actinobacteria were the most abundant bacteria in the samples. The domain Archaea was represented
mainly by methanogenic genera Methanothrix and Methanosarcina and the order Methanomassiliicoccales.
Exposure to antibiotics inhibited the growth and development of methanogenic microorganisms in the
substrate. Antibiotics also influenced the abundance and prevalence of ARGs in samples. Seventeen
types of ARGs were identified and classified. Genes encoding resistance to tetracyclines, macrolide–
lincosamide–streptogramin antibiotics, and aminoglycosides, as well as multi-drug resistance genes,
were most abundant. Antibiotics affected homoacetogenic bacteria and methanogens, and decreased
the production of CH4 . However, the antibiotic-induced decrease in CH4 production was minimized
in the presence of highly drug-resistant microorganisms in AD bioreactors.
Keywords: anaerobic digestion; antibiotics; biodiversity; cattle manure; synergistic effect
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1. Introduction
Copyright: © 2022 by the authors.
Licensee MDPI, Basel, Switzerland.
This article is an open access article
distributed under the terms and
conditions of the Creative Commons
Attribution (CC BY) license (https://
creativecommons.org/licenses/by/
4.0/).
Methane fermentation (anaerobic digestion, AD) is a promising technology for stabilizing organic matter, including cattle manure from livestock production [1]. Anaerobic
digestion leads to the production of environmentally friendly biogas containing methane
(CH4 ) as well as digestate (D ) [2]. Digestate is used mainly as organic fertilizer in agriculture [3]. However, antibiotics are widely used in livestock farms to promote animal growth,
prevent disease and treat bacterial infections [4]. The use of antibiotics as growth promoters
has been banned worldwide, excluding in China and Brasil. In the European Union, the
use of bacteriostatic agents as growth promoters or feed additives in livestock production
was banned in 2003 (Regulation (EC) No. 1831/2003 of 22 September 2003) [5]. Despite
Energies 2022, 15, 1920. https://doi.org/10.3390/en15051920
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the above, antimicrobials are still overused in agriculture, in particular in the livestock
industry [6]. Broad-spectrum bacteriostatic drugs are most frequently used in agriculture
and veterinary medicine [7]. The most popular classes of antibiotics include beta-lactams
(such as amoxicillin, AMO) [8], fluoroquinolones (such as enrofloxacin, ENRO) [9], and
nitroimidazole derivatives (such as metronidazole, MET) [10]. These antimicrobials inhibit
the AD process, induce changes in microbial communities, promote the spread of drug
resistance (DR), and influence the efficiency of biogas and CH4 production [11]. Research
has demonstrated that fluoroquinolones are highly persistent in the environment, and that
the efficiency of fluoroquinolone removal during AD is close to zero [12]. In the livestock
industry, MET is used mainly to treat infections caused by anaerobic bacteria [13]. This
antimicrobial can be accumulated for up to 42 days in the host organism [10]. The main
metabolic pathway of MET involves the oxidation of two side chains of the imidazole ring
and glucuronidation. Metronidazole can be introduced to AD bioreactors with feces, and it
can spread to the environment when soil is fertilized with digestate [14]. Amoxicillin is not
highly persistent in the environment due to its specific chemical structure and the presence
of a ring that is easily degraded by H+ , OH- , Ca2+ , Mg2+ and Fe2+ ions [15]. However,
even trace amounts of drug transformation products (TPs) in the environment can promote
the spread of antibiotic resistance [16]. The presence and spread of broad-spectrum betalactamases in the environment pose a particularly serious threat to public health around
the world [17].
Most antimicrobial substances detected in cattle manure are composed of several
compounds. The above can be attributed to the fact that pharmaceuticals are widely used
in livestock production and are excreted with urine and feces [18]. The overuse of antibiotics
in the livestock industry has contributed to DR and the transmission of antibiotic resistance
genes (ARGs) in the environment. Drug resistance also promotes the spread of ARGs in AD
bioreactors where cattle manure containing drug residues is fermented [19]. The long-term
synergistic effects of antibiotics and other parameters of the AD process on the fate of ARGs
have not been fully elucidated because AD involves complex microbial communities that
degrade chemical compounds and produce biogas and CH4 . Antibiotics indirectly influence
methanogenic bacteria [20], but the relationships between methanogenic Archaea, bacteria,
ARGs, and CH4 production remain insufficiently investigated. Anaerobic digestion can
pose a serious threat to public health, and it can contribute to the transmission of ARGs in
the environment and the spread of DR, which is why the safety of the AD process should be
thoroughly analyzed. Antibiotic resistance genes have been classified as persistent organic
pollutants that are more harmful to the environment than antibiotics, which also gives
serious cause for concern [21]. According to [22], human activities, expressed by the size
of livestock populations in industrial farms, significantly influence the ARG profile in the
environment, including in drinking water. Water contaminated with ARGs is administered
to livestock, cattle manure is fermented in bioreactors, and the resulting digestate is used as
agricultural fertilizer, which completes the cycle of acquisition and spread of ARGs in the
environment. Research has demonstrated that the copy numbers of various ARG groups
can increase in response to specific parameters of the AD process [23]. The associated
risks require in-depth analysis, especially since the long-term synergistic effects of several
antibiotics on the AD process have been poorly researched in the literature. The literature
from the last decade in which the synergistic effect of drugs on the mesophilic AD process
was investigated is summarized in Table 1.
The aim of the present study was to determine the long-term synergistic effects of a
combination of AMO, ENRO and MET on mesophilic AD of cattle manure, including the
efficiency of CH4 production and the accumulation of volatile fatty acids (VFAs). Changes
in the structure of microbial communities that participate in AD, and the spread and fate
of ARGs were also examined. These parameters were analyzed in response to different
combinations of antibiotics, different antibiotic concentrations, and different periods of
antibiotic exposure. The combined effect of organic pollutants such as antibiotics may pose
ecological risks and influence ARG profile in the environment. The study will provide
Energies 2022, 15, 1920
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valuable insights into changes in the succession of methanogenic communities in fermented
biomass during long-term exposure to antibiotics. The results will be used to identify the
main problem areas and propose effective solutions for improving the efficiency of ARGs
removal from digestate. The environmental threats associated with the spread of ARGs
from digested cattle manure were also evaluated. The study will contribute valuable information to the existing knowledge base, which can be useful in reducing environmental
pollution with ARGs. This study evaluates the anaerobic digestion environmental impacts of antibiotics to make the integration process more environmentally sustainable and
identifies challenges and future prospects. The study relied on metagenomic techniques,
which are the most effective tools for characterizing microbial communities and analyzing
changes in microbial biodiversity.
Table 1. The summary of the literature from the last decade, about synergistic effect of drugs on the
mesophilic AD process.
Kind of
Substrate
Antibiotics Used in
Investigate
Antibiotics Combinations
Concentration
Effect of Antibiotics
Seed sludge
Short-term effect of
sulfamethoxazole and
tetracycline,
erythromycin and
sulfamethoxazole,
erythromycin and tetracycline
0, 2, 20, 50, 100, 250, and
500 mg/L
Inhibition of CH4 production in
reactors fed with
erythromycin-sulfamethoxazole
and sulfamethoxazole-tetracycline
and weak inhibition of CH4
production in reactors fed with the
mixture of
erythromycin-tetracycline
[24]
Synthetic
wastewater
Short-term effect of three
antibiotics with four
combinations;
sulfamethoxazole-tetracycline;
erythromycinsulfamethoxazole;
erythromycin-tetracycline and
erythromycin-tetracyclinesulfamethoxazole
0, 1, 10, 25, 50, 100 and
250 mg/L
Inhibition of biogas production;
microorganisms’ development of
resistance to antibiotics
[25]
Synthetic
wastewater
Short-term effect of
erythromycin and
sulfamethoxazole mixture
In 10 stages, respectively
(mg/L): 0.1 and 0.5; 0.2 and
5; 0.5 and 5; 0.5 and 10; 1 and
10, 1 and 15; 1.5 and 15; 1.5
and 20; 2 and 20; 2.5 and 25;
Inhibition of biogas production;
microorganisms’ development of
resistance to antibiotics
[26]
Synthetic
wastewater
Long-term effect of
erythromycin-tetracyclinesulfamethoxazole and
sulfamethoxazole-tetracycline
0.5; 5; 10; 15; 20; 25; 40 mg/L
for SMX; 0.1; 0.2; 0.5; 1; 1.5; 2;
2.5; 3 mg/L for
erythromycin-tetracycline
Increasing antibiotic
concentrations has a negative
impact on the microbial
community structure and function
in anaerobic wastewater treatment;
increase of AR
[27]
Amoxicillin, metronidazole,
and ciprofloxacin
Static conditions—In first
variant, respectively
[mg/kg]; 2, 16 and 1024, in
second variant: 1, 8, and 512;
and last variant: 0.25, 2, and
512, semi-continuous
conditions, respectively: 16,
8, and 2 mg/kg
Synergistic effect of antibiotics
causes inhibition of CH4
production and accumulation of
VFAs
[28]
Sewage sludge
from a
municipal
WWTP
References
Energies 2022, 15, 1920
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2. Materials and Methods
2.1. Experimental Setup and Sampling
Cattle manure was subjected to AD in 2 L digesters operating under dynamic, semicontinuous conditions. The process digester was fed with substrate containing a mixture of
AMO, ENRO and MET. The antibiotics were chosen based on the results of our previous
research [23]. In the process bioreactor, biomass was subjected to AD in the presence
of AMO, ENRO and MET. In the control bioreactor, biomass was fermented without
antibiotics. In the process bioreactor, AD was conducted in seven experimental series
(I–VII) that differed in the concentrations of the antibiotics added to biomass Table 2.
Antibiotic concentrations were gradually increased in successive experimental series.
Table 2. Antibiotic concentrations (µg/mL D ) and ID numbers of the samples collected from the
experimental reactor (experimental series I–VII) and the control reactor (CS) without antibiotics.
Experimental
Series
Antibiotic Concentrations (µg/mL D )
AMO
ENRO
MET
Series I
1
0.25
0.25
Series II
2
0.5
0.5
Series III
2.5
0.75
0.75
Series IV
5
1.5
1.5
Series V
10
3
3
Series VI
16
4
4
Series VII
32
8
8
Collected
Samples
Sample ID
Sample 1
Sample 2
Sample 3
Control sample
Sample 1
Sample 2
Sample 3
Sample 1
Sample 2
Sample 1
Sample 2
Control sample
Sample 1
Sample 2
Sample 1
Sample 2
Sample 3
Sample 1
Sample 2
Sample 3
Control sample
S1 I
S2 I
S3 I
CS I
S1 II
S2 II
S3 II
S1 III
S2 III
S1 IV
S2 IV
CS IV
S1 V
S2 V
S1 VI
S2 VI
S3 VI
S1 VII
S2 VII
S3 VII
CS VII
Cattle manure was collected in the field at the Agricultural Experiment Station in
Bałdy, Poland, operated by the University of Warmia and Mazury in Olsztyn. The collected
manure was stored at a temperature of 5 ◦ C until analysis. The analyzed substrate had
the following characteristics: total solids (TS)—107.5 ± 29.0 mg TS/g; volatile solids (VS)—
84.2 ± 22.2 mg VS/g; pH—7.75 ± 0.4; total phosphorus (TP)—1.0 ± 0.3 mg TP/g of TS;
total nitrogen (TN)—4.1 ± 1.6 mg TN/g of TS. The inoculum (anaerobic sludge) was
obtained from a laboratory methane fermentation reactor fed with cattle manure and Sida
hermaphrodita silage. Anaerobic sludge had the following characteristics: 35.2 ± 4.8 mg
TS/g; 23.2 ± 2.1 mg VS/g; pH of 7.9 ± 0.9; 0.8 ± 0.6 mg TP/g of TS; 5.0 ± 0.9 mg TN/g of
TS. The digester was operated at a daily organic loading rate of 2.8 kg × m−3 × d−1 .
Hydraulic retention time (HRT) was 28 days. The digesters were equipped with
mechanical stirrers, feeding and discharge systems, and they were coupled with the Automatic Methane Potential Test System (AMPTS II, Bioprocess control, Lund, Sweden)
which measured CH4 production. Gas was normalized for standard temperature (273.2 K)
and pressure (1.01325 bar). The AD process was conducted at mesophilic temperature
(37 ◦ C), and the substrate was stirred for 30 s at 100 rpm at 10min intervals. The experiment
lasted 417 days, with two replicates per bioreactor. To monitor the digestion process, the
substrates were sampled twice a week to determine their pH, FOS/TAC ratio (the FOS
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value denotes VFA content, and the TAC value denotes the estimated buffer capacity of the
sample), and the content of TS, VS, TN and TP.
The content of VFAs was determined with the use of a gas chromatograph (Brüker,
450-GC) with a flame ionization detector (FID) based on a previously described method [29].
FOS/TAC ratio was determined with the TitraLab AT1000 Series Titrator (Hatch). The
content of TS and vs. in biomass samples was determined according to APHA [30]. The
content of TN and TP in mineralized samples was determined in HachLange cuvette tests.
All measurements were performed in duplicate.
Microbial diversity was determined by metagenomic analysis at the beginning, in the
middle and at the end of the AD process in seven experimental series. For this purpose,
digestate samples were collected in the first week of AD from each experimental series
(sample No. 1), in the middle of each experimental series (sample No. 2) and in the last week
of each experimental series (sample No. 3). At least two digestate samples were collected
in duplicate in each experimental series. The samples were numbered (1 to 3) and labeled
with the number of the corresponding experimental series (I to VII) based on increasing
concentrations of the tested antibiotics Table 1. The concentrations of the antibiotics added
to the experimental digester increased after doubling the digester’s hydraulic volume. The
collected samples and the adopted nomenclature are described in Table 1. The substrate
fed to the control digester (two replicates) was not supplemented with antibiotics (control
samples, CS); Table 1. To compare changes in the structure of microbial communities during
the AD process, control samples were collected from experimental series I at the beginning
of AD, from series IV in the middle of AD, and from series VII at the end of AD.
2.2. Genomic DNA Isolation
Total DNA was isolated in triplicate from digestate samples of 1 g collected from each
reactor using the MP Biomedicals™ FastDNA™ SPIN Kit for Soil (MP Biomedicals™, Solon,
OH, USA). DNA was isolated according to the manufacturer’s instructions. The quality and
yield of the extracted DNA were verified with the NanoDrop spectrophotometer (Thermo
Fisher Scientific, Waltham, MA, USA) and the Qubit fluorometer (Thermo Fisher Scientific,
Waltham, MA, USA).
2.3. DNA Sequencing
The DNA from each sample was used to construct a shotgun library with the TruSeq
Nano DNA Library Kit for Illumina (Macrogen, Amsterdam, The Netherlands) with pairedend 2 × 150 bp sequence reads and 350 bp insert. Binary base call (BCL) files were converted
to FASTQ with the bcl2fastq Illumina package. The prepared libraries were sequenced on
the NovaSeq6000 Illumina platform. Twenty-one DNA samples generated approximately
3.3 Gbp of metagenomic data, and the entire dataset had a size of 144.1 Gbp. Metagenomics
datasets were deposited in the European Nucleotide Archive (ENA) database under accession numbers PRJEB48924. The quality of paired-end metagenomic sequences were
evaluated in the Kneaddata v. 0.7.6 software (https://github.com/biobakery/kneaddata,
accessed on 12 November 2021). In the first step, low-quality and rich adapter sequences
were filtered with the Trimmomatic tool [31] in the Kneaddata v. 0.7.6 software (Huttenhower Lab, Harvard Chan Center for the Microbiome in Public Health, Boston, MA,
USA) pipeline based on the following parameters ‘2:30:10:8:TRUE SLIDINGWINDOW:4:20
MINLEN:75′ . In the second step, the reads were aligned to bovine contaminants with a
known reference genome (NCBI GenBank accession No. GCA_000003055.5, accessed on
12 November 2021). Unmapped sequences were classified for metagenomic analyses. To
determine bacterial distribution the remaining reads were mapped to bacterial reference
sequences using bowtie2 software v. 2.4.5, (accessed on November 2021) [32]. Bacterial
diversity was estimated by Metaphlan v. 2.0 (Huttenhower Lab) [33] and visualized by
circlize [34] packages in R v. 4.0.2 (R Core Team, 2017, Vienna, Austria). The Kneaddata and
Metaphlan software packages were used as components of the Biobakery v.0.15.1 pipeline
(https://github.com/biobakery/biobakery_workflows, accessed on 12 November 2021).
Energies 2022, 15, 1920
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The abundance of ARGs was determined based on the number of trimmed paired-end
reads in ARG-OAP v.2.0 software (Environmental Microbiome Engineering and Biotechnology Laboratory, The University of Hong Kong) [35]. The number of ARG-like sequences
was normalized to the number of metagenome and ARG sequences in each sample to
compare ARG levels across digestate samples. ARG levels were expressed in terms of
“total metagenome sequences” (reads per million reads, ppm) [36] or “total ARG-like
sequences” (%).
2.4. Statistical Analysis
Statistical analyses were performed in the Statistica program (ver. 13.1., StatSoft,
Kraków, Poland, accessed on 10 December 2021). Data were visualized with the use
of GraphPad Prism software (GraphPad Software, CA, USA). The correlations between
CH4 production, microorganisms, ARG types, and VFA production were determined by
calculating Spearman’s rank correlation coefficients at a significance level of p ≤ 0.05.
3. Results and Discussion
3.1. Long-Term Synergistic Effects of AMO, ENRO and MET on CH4 Production and
VFA Concentrations
Anerobic digestion is a process composed of four mutually dependent stages: hydrolysis, acidogenesis, acetogenesis and methanogenesis [37]. Bacteria and methanogenic
microorganisms are responsible for the efficiency of CH4 production during AD. The first
three stages of AD involve bacteria, whereas methanogens are responsible for the last stage
of the process and CH4 production [11]. Bacteria and methanogens enter into syntrophic
interactions to produce the required substrates for growth and development. These interactions are essential to maximize CH4 yields [26]. The efficiency of CH4 production
is determined by numerous factors, including the type of added antibiotics, antibiotic
concentrations, temperature inside AD bioreactors, and duration of AD [38,39].
The effects of long-term exposure to increasing concentrations of a mixture of AMO,
ENRO and MET on the inhibition of CH4 production in manure digestates were analyzed
in seven experimental series; see Section 2.1 and Figure 1. This approach was adopted to
determine the long-term influence antibiotics on the efficiency of CH4 production. Methane
production was expressed in liters per kilogram of volatile solids (L/kg VS).
Figure 1. Methane production in seven experimental series (L/kg VS). The presented data are the
average values in each experimental series with triplicate measurements and two replicates. Error
bars represent standard deviation (SD).
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Methane production was somewhat higher (3 L/kg vs. per sample) in the experimental
samples containing a mixture of AMO, ENRO and MET than in control samples (ANOVA,
Kruskal–Wallis, p > 0.05); Figure 1. In the first few weeks of the AD process, CH4 yields were
high at around 90 L/kg vs. in the control sample from series I (CS I) and in the experimental
samples from series I and II (Supplementary Materials, Table S1). The above trend was
maintained until the end of experimental series II, during which AMO, ENRO and MET
were added to the bioreactor at concentrations of 2, 0.5 and 0.5 µg/mL D , respectively;
Table 2.
In experimental series III, Figure 1, a sudden decrease (ANOVA, Kruskal–Wallis,
p > 0.05) in CH4 production was observed in experimental samples S1 III and S2 III Table S1.
Methane production was approximately 40% lower in comparison with series I (approximately 90 L/kg VS) and series VII when CH4 production peaked (108.2 L/kg VS). This
trend was maintained until the end of series IV. The above experimental series were conducted in December, January, February, March and the first half of April; Table S2. In
these months, livestock diets are often modified due to the lower availability of nutrients
from fresh fodder [40,41]. In winter, the prevalence of infections is also higher, and antimicrobials are more frequently used in livestock farming [42]. Therefore, the presence
of chemical compounds such as ammonia in biomass could have inhibited the growth
and development of bacteria and methanogens in the analyzed digestates [11]. Specific
bacterial groups supply substrates that are used by methanogenic microorganisms in the
production of CH4 [43]. Therefore, the sudden drop in CH4 yields in series III and IV,
Figure 1, and the absence of significant differences (ANOVA, Kruskal–Wallis, p > 0. 05) in
CH4 production could be attributed to periodic disruptions in AD and the low supply of
substrates that are essential for microbial growth and development in fermented biomass.
In conclusion, these unfavorable process conditions temporarily inhibited the growth and
development of methanogens and, consequently, decreased CH4 production in both control
and experimental samples.
Methane production peaked in experimental series VII when digestates were supplemented with the highest concentrations of the tested antibiotics (AMO—32 µg/mL D ,
ENRO—8 µg/mL D , MET—8 µg/mL D ) Table 1. In series VII, CH4 yields were somewhat
higher in the experimental sample (108.2 L/kg VS; SD = 15.2) than in the control sample
(105.3 L/kg VS; SD = 13).
The CH4 production curves for the experimental samples and the control samples
were similar throughout the entire AD process; Figure 1. These results indicate that antimicrobials exerted a temporary effect on CH4 production. Probably, biomass microorganisms
could have probably easily adapted to the applied drug concentrations due to the high
supply of antibiotics in livestock farming [44]. Acquired antibiotic resistance decreased
the tested drugs’ inhibitory effect on the growth of microbial groups involved in CH4
production and, consequently, on the efficiency of biogas production. According to some
authors, antibiotic-resistant bacteria (ARB) and ARGs are naturally present in cattle gut
microbiota; they are excreted with feces and transferred to digestates during AD [45,46]. In
fermented substrates, DR can spread via horizontal gene transfer (HGT) [47], and it can
ultimately decrease antibiotics’ inhibitory effect on CH4 production. This hypothesis was
confirmed by the results of the metagenomic analysis which revealed high abundance and
diversity of the examined ARGs Section 3.3 in fermented biomass in different stages of
the experiment. In our previous study, the presence of antibiotics in cattle manure clearly
influenced CH4 production, but antimicrobials were administered to bioreactors at much
higher doses than in the present experiment. In the cited study, AMO and oxytetracycline
applied at a concentration of 512 µg/mL D and MET and sulfamethoxazole applied at a
concentration of 1024 µg/mL D clearly inhibited CH4 production [48]. According to other
researchers, antimicrobials significantly affect AD, but only after a certain threshold concentration of a drug has been achieved [49,50]. In the work of Wen et al. [51], sulfamethoxazole
administered at 50 µg/mL TS exerted a minor influence on CH4 production. Yin et al. [52]
found that biogas production began to decrease when oxytetracycline and chlortetracycline
Energies 2022, 15, 1920
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concentrations exceeded 40 and 60 mg/kg TS, respectively. Antibiotics had no significant
effect on biogas production when digestates were exposed to oxytetracycline concentrations below 40 mg/kg TS and chlortetracycline concentrations below 60 mg/kg TS [52].
Other published findings are consistent with the results of this study, where the highest
concentrations of the tested antimicrobials were 32 µg/mL D for AMO and 8 µg/mL D for
ENRO and MET. In the present study, antibiotics induced a minor and temporary decrease
in CH4 yields in experimental series III and IV, which could be attributed to changes in
methanogen biodiversity. These changes could have resulted from the limited availability
of substrates for CH4 production, the presence of toxic substances in the bioreactor, high
microbial loads, and temporary disruptions in the physicochemical parameters of the AD
process [53].
3.2. Concentrations of Volatile Fatty Acids
The products of protein and carbohydrate hydrolysis, such as VFAs, including acetic,
propionic, isobutyric, butyric, isovaleric, valeric, isocaproic and caproic acids and heptane,
play an important role in AD [54]. In the current study, VFA concentrations were measured
in each experimental series throughout the entire 417-day experiment. A minor increase
(ANOVA, Kruskal–Wallis, p > 0.05) in acetate production was observed at the beginning of
the AD process in experimental series I (approximately 6 g/L D ); Figure 2.
Figure 2. Average concentrations of VFAs (g/L D ± SD) in the experimental samples collected from
series I–VII. Control samples without AMO, ENRO and MET are marked as CS and are labeled with
the number of the corresponding experimental series (I–VII).
A minor increase (ANOVA, Kruskal–Wallis, p > 0.05) in the concentrations of acetic
acid (approximately 13 g/L D ) and propionic acid (approximately 6 g/L D ) was noted
in experimental series VII; Figure 2. The content of isovaleric and isobutyric acids also
increased (from 3 g/L D to nearly 5 g/L D ) in the samples collected during experimental
series VII when digestates were exposed to the highest antibiotic concentrations; Figure 2
Energies 2022, 15, 1920
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(ANOVA, Kruskal–Wallis, p > 0.05). The concentrations of most of the remaining VFAs
did not exceed 3 g/L D . The increase in VFA content could have resulted from high
antibiotic concentrations in series VII, i.e., 32 µg/mL D for AMO and 8 µg/mL D for ENRO
and MET. However, the observed increase in the content of acetate, which is utilized by
microorganisms of the genera Methanosarcina and Methanothrix to produce CH4 in different
stages of AD, appears to be a natural phenomenon [55,56]. Methane yields were high in
the last experimental series, which suggests that microorganisms relied on increased VFA
concentrations to produce CH4 during methanogenesis [57].
3.3. Long-Term Synergistic Effects of AMO, ENR and MET on the Microbial Biodiversity
of Digestates
3.3.1. Bacteria
A total of 2 × 1,049,430,401 high-quality paired-end sequences were obtained from
21 biomass samples exposed to increasing concentrations of AMO, ENRO and MET over a
long period of time; Table 2. The number of sequences per sample ranged from 47,053,977
to 51,020,960. The sequences were grouped between 23 and 54 OTUs at 97% similarity level,
respectively, for the least and most abundant samples. It was assumed that the structure
of microbial communities in digestates would be similar to the cattle gut microbiome,
which is significantly influenced by, among other things, the presence of pharmaceuticals
in feed. The duration of the experiment was yet another factor that induced changes in the
composition of microbial consortia during AD. As a result, bacterial OTUs in digestates
varied considerably subject to the antibiotic dose and the duration of the AD process.
Eight bacterial phyla were identified in digestates during the AD process and at the
end of the 417-day experiment. These were: Bacteroidetes (Bacteroidia class), Firmicutes
(Bacilli, Clostridia, Mollicutes, and Erysipelotrichia classes), Proteobacteria (Alphaprotebocateria,
Betaproteobacteria, Gammaproteobacteria, Deltaproteobacteria and Epsilonproteobacteria classes),
Acidobacteria (Blastocatellia class), Spirochaetes, Synergistetes (Synergistia class) Actinobacteria
and Tenericutes; Figure 3. Firmicutes and Bacteroidetes are the dominant phyla during AD [58].
Bacteroidetes are well-known proteolytic bacteria [59], whereas Proteobacteria are among the
key consumers oxidizing long-chain VFAs during AD [60]. Soil-dwelling Actinobacteria
degrade various organic compounds and xenobiotics, whereas Acidobacteria are obligate
anaerobes that ferment aromatic compounds and acetates [61]. Synergistetes and Spirochaetes
convert products such as propionate, butyrate, isobutyrate, valeric acid, isovaleric acid and
ethanol to acetate, H2 and CO2 . The resulting products are used by methanogens in CH4
production [62].
The microbial community was represented mainly by Bacteroidetes species, which
accounted for 89% of the bacteria in experimental series I (samples S1 I, S2 I, S3 I) and more
than 70% of the bacteria in experimental series II (S1 II, S2 II, S3 II); Figure 3. In comparison
with the experimental samples from series I and II, the proportion of Bacteroidetes decreased
to 50% in series III (S1 III, S2 III). Bacteroidetes also accounted for 50% of the bacteria in
the control sample from series I. The proportion of Bacteroidetes was also determined to be
50% in samples S2 VII and S3 VII collected during experimental series VII. The abundance
of Bacteroidetes in samples S2 IV, S1 VI, S2 VI and S3 VI from experimental series IV and
VI did not exceed 30%. In the remaining experimental samples and in control samples,
the abundance of Bacteroidetes was estimated at 20%. Interestingly, the proportion of
Bacteroidetes in most experimental samples ranged from 30% to 50%, but it was determined
to be nearly 20% in control samples. This observation suggests that Bacteroidetes species
were highly resistant to the tested antimicrobials [63]. Bacteroidetes widely colonize the
gastrointestinal tract of cattle, and they are ubiquitous in manure [64].
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Figure 3. Circos presenting the (a) most abundant bacterial consortia in digestate samples and
(b) most abundant Archaea consortia in digestate samples. The OTU values of the presented species
exceeded 1 ppm.
Acidobacteria were also highly prevalent in the microbial community colonizing cattle
manure digestates; Figure 3. In experimental series I, Acidobacteria accounted for 1% to
3% of the bacteria identified in the experimental samples (S1 I, S2 I, S3 I), whereas their
share in the control sample (CS I) exceeded 11%. The proportion of Acidobacteria species
in fermented biomass continued to increase in successive weeks of the experiment, and
it exceeded 50% in sample S2 II in series II. The share of Acidobacteria reached up to 60%
in samples S3 II, S1 III, S2 III and S1 IV. In the control sample from series IV (CS IV),
Acidobacteria also represented around 60% of the microbial community. In series V, the
proportions of Acidobacteria in sample S2 V decreased rapidly to around 20%, and this
trend was maintained in the experimental samples containing a mixture of AMO, ENRO
and MET until the end of AD. In the control sample collected in the last stage of the
AD process in series VII, Acidobacteria accounted for 64% of the microbial community.
These results suggest Acidobacteria were resistant only to lower concentrations of the tested
drugs. Prolonged exposure to antimicrobials increases the risk of selection pressure and
the spread of ARGs among microorganisms [65]. Therefore, the use of digestates as
agricultural fertilizers can contribute to the transfer and dissemination of ARGs in the soil
environment [15,66]. Other authors [67] have reported growing levels of DR in endophytes
colonizing lettuce roots, leaves and the phyllosphere in fields fertilized with manure, and
the observed changes in the plant resistome were correlated with bacterial taxa such as
Acidobacteria, Proteobacteria and Firmicutes, which were also identified in the present study.
Bacteria of the phylum Firmicutes accounted for 4% to 8% of the microorganisms in
samples S1 I, S2 I and S3 I from experimental series I; Figure 3. In the control sample
collected from series I, more than 17% of the bacterial community was represented by
Firmicutes species. In series II and III (samples S1 II, S2 II, S3 II, S1 III and S2 III), the proportion of Firmicutes ranged from 9% to 12%. The share of Firmicutes was estimated at 12%
to around 20% in the samples collected in series IV, V and VI. Interestingly, in experimental
series VII, Firmicutes accounted for 23% of the microorganisms in the experimental samples,
but for only 8% in the control sample. Firmicutes can easily degrade complex polysaccharide
and protein substrates under anerobic conditions, and synthesize acetate from amino acids
that are produced during protein hydrolysis [11,68]. This bacterial phylum is predominant
in the gastrointestinal tracts of humans and animals, and it is also ubiquitous in untreated
wastewater, which suggests that Firmicutes species are highly resistant to antimicrobials [63].
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Huerta et al. [69] concluded that Firmicutes probably harbor and transmit ARGs in the
environment, including in aquatic ecosystems. According to Shi et al. [70], Firmicutes are
the main ARG hosts in agricultural soils. Other authors have shown in previous studies
that bacteria can acquire resistance to selected antimicrobial agents (tetracycline, streptomycin or sulfonamide) without any contact with these drugs [71]. It is also a problem that
resistant bacteria and ARGs can persist for years, even with short-term administration of
antibiotics [72]. In addition, it is noteworthy that ARGs can be horizontally transferred
between microbes through MGEs. The HGT of ARGs can occur between nonpathogens,
pathogens, and even distantly related organisms [73,74]. Recent studies have demonstrated
specific instances of the HGT of ARGs in human and animal guts, soil, sediments, and
water [75,76].
3.3.2. Archaea
The abundance of the Euryarchaeota species in digestate samples differed considerably across experimental series in the AD process; Figure 3. In most samples, the
predominant methanogens were bacteria of the genera Methanothrix and Methanosarcina
and order Methanomassiliicoccales. The genus Methanothrix is composed of acetoclastic
methanogens [54] that are sensitive to unfavorable environmental conditions, whereas
Methanosarcina spp. use various substrates, including acetate, H2 and methyl compounds [77].
Methanothrix soehngenii, Methanosarcina mazei and Methanomassiliicoccales archaeonRumEnM2 were the dominant species in both experimental and control digestate samples.
Methanobrevibacter millerae was additionally identified in five experimental samples containing a mixture of AMO, ENRO and MET (S3 I, S2 II, S3 II, S1 III and S3 VII), and in two
control samples (CS IV and CS VII). Methanosarcina thermophila was detected in the experimental samples collected in series I, II and III. The growth of Methanosarcina thermophila
was probably inhibited due to unfavorable conditions during prolonged AD as well as the
bacterium’s sensitivity to the applied combination of drugs [78]. Methanosarcina thermophila
was not identified in successive experimental series in which antibiotic concentrations were
higher, which suggests that prolonged exposure to antimicrobials can decrease the diversity
of methanogenic communities in biomass. Methanosarcina mazei was also abundant in
the experimental samples collected in series I–III, but its prevalence decreased rapidly in
response to higher antibiotic concentrations in series IV, and it remained low until the end
of the AD process.
3.4. The Effects of Antibiotics on the Total Abundance of ARGs and Resistant Types
A total of 401 ARG subtypes belonging to 17 ARG types that encode resistance to
bleomycin, kasugamycin, trimethoprim, polymyxin, fosfomycin, quinolone, rifamycin,
fosmidomycin, chloramphenicol, beta-lactam, sulfonamide, vancomycin, bacitracin, aminoglycoside, macrolide–lincosamide–streptogramin (MLS) antibiotics, and tetracycline, as
well as multidrug resistance, were identified in manure digestates; Figure 4. Genes conferring resistance to MLS antibiotics (32.6%), tetracycline (22.7%), and aminoglycosides
(19.5%), as well as genes encoding resistance to multiple drugs (10.3%), were most abundant
in digestate samples; Figure 4. The abundance of the remaining ARG types in digestate
samples did not exceed 6%.
The most prevalent ARG subtypes encoding resistance to MLS drugs were ermF, lnuB,
lsa, macA, macB, and mef A; Figure 5. At the end of the 417-day experiment, a minor increase
was observed in the abundance of the ermF gene, from 23 ppm in series I to 25 ppm in
series VII. The ermF gene encodes 23S rRNA adenine-specific N-6-methyltransferases that
methylate bacterial 23S rRNA. Methylation prevents MLS drugs from binding to bacterial
ribosomes and, consequently, encodes resistance to this group of antibiotics [79,80]. The
ermF gene is one of the most prevalent ARGs conferring resistance to MLS antibiotics, and
it is also one of the major acquired resistance genes in bacteria [81]. An increase in ermF
abundance in digestates can contribute to the spread of other ARGs in the environment via
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HGT because in addition to the ermF gene, tet(X1) and tet(X2) genes were also identified on
conjugative transposon CTnDOT [82].
Figure 4. Percentage (%) distribution of different ARG types in digestate samples. MLS—macrolide–
lincosamide–streptogramin antibiotics.
Figure 5. Heatmap presenting the abundance (ppm) of ARG subtypes in the experimental samples
(S1, S2, S3) collected from seven experimental series (I–VII) and in control samples (CS).
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The dominant tetracycline resistance genes were tet32, tet36, tet44, tetM, tetO, tetP,
tetQ, tetT, tetW, tetX2 and tetracycline_resistance_protein. These ARG subtypes encode two
mechanisms of specific tetracycline resistance. tet32, tet36, tet44, tetM, tetO, tetP, tetQ,
tetT and tetW genes are linked with ribosomal protection proteins (RPP), whereas tetX2
encodes a tetracycline-degrading enzyme [83]. The RPP mechanism is more ubiquitous
in the environment, which explains the presence of the identified tetracycline resistance
genes in this study. In the work of Santamaria et al. [84], genes encoding RPP were also
most abundant in cattle manure. Numerous researchers have reported that cattle manure
is a reservoir of ARGs encoding RPP. Therefore, the AD of cattle manure contributes to
the spread of tet genes in bioreactors and crop fields. This observation was confirmed by
Chen et al. [85] and Wu et al. [86], who identified numerous tetracycline resistance genes in
topsoil samples collected from arable fields.
The most prevalent aminoglycoside resistance genes were aad(6), aadA, aadE, ant(9)-I,
aph(3′ ”)-III, aph(3′ ’)-I and aph(6)-I. These putative genes encode O-nucleotidyltransferases,
i.e., aminoglycoside-modifying enzymes. This enzymatic modification process is one of the
most common DR mechanisms in the environment [87]. Progressive DR and the spread
of ARGs reduce the efficacy of aminoglycosides. In several medical reports, the identified
bacteria were totally resistant to aminoglycosides, rendering these drugs completely useless
in pharmacotherapy [88].
The most abundant multidrug resistance genes were TolC, adeJ, adeK, mexB, mexT,
multidrug_ABC_transporter, multidrug_transporter and oprM. The adeJ gene is responsible
for drug recognition and proton motive force generation that provides the cellular energy
required for substrate transport [89]. TolC belongs to the resistance–nodulation–division
(RND) family of transporters, and it confers resistance to chloramphenicol, aminoglycoside,
macrolide, acriflavine, doxorubicin, erythromycin, puromycin and beta-lactams [90]. Two
of the detected genes, mexB and mexT, are most often identified in clinical isolates, which
gives serious cause for concern [91]. The presence of these genes in cattle manure digestates
indicates that mexB and mexT are being spread from the hospital setting to the natural
environment and agriculture [8].
Interestingly, despite the fact that AMO was one of the tested antibiotics, cfxA and
OXA-209 were the only beta-lactamase resistance genes in the digestate samples. In experimental series I, the abundance of cfxA and OXA-209 exceeded 1 ppm, but in successive
series, their abundance decreased rapidly to 0.26 ppm and 0.02 ppm. Beta-lactams have an
unstable ring and they are not highly persistent in the environment, which could explain
the low abundance of genes encoding resistance to this class of antibiotics [92].
The total number of sequences characteristic of the identified ARGs was higher in the
experimental samples containing a mixture of antibiotics, but numerous ARG sequences
were also identified in control samples. The abundance of beta-lactam resistance genes
was reduced by 50%. However, the prevalence of genes encoding resistance to tetracyclines, aminoglycosides and MLS drugs increased considerably in digestate samples. The
abundance of ARGs in the experimental samples (with the addition of AMO, ENRO and
MET) and control samples is worrying because it indicates that the spread of ARGs in cattle
manure is a process that had begun before AD. However, experimental and control samples
of cattle manure digestates differed significantly in their ARG profiles, which indicates that
ARGs are transferred via various pathways in the presence of antibiotics. The analyzed
samples differed in the prevalence of ARG subtypes. Both the abundance and diversity
of ARGs were much higher in the experimental samples with the addition of antibiotics
than in the control samples. In a study evaluating the influence of drugs on AD, Wen
et al. [51] also reported an increase in the abundance of individual ARGs during AD, and
concluded that microbial communities and mobile genetic elements played the key role in
the transmission of ARGs and an increase in their abundance. The fact that ARGs can reach
other pathogenic microorganisms via HGT [63] is particularly worrying. It can endanger
the efficacy of the available antibiotics, thus increasing the prevalence of infections caused
by pathogens that do not respond to pharmacotherapy [93].
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3.5. Results of Statistical Analyses
The correlations between microbial abundance and ARG abundance were determined
by calculating Spearman’s rank correlation coefficient (R > 0.7; p < 0.01); Figure 6, Table S3.
Figure 6. Spearman’s rank order correlation coefficients for the relationships between microbial
abundance and the abundance of different ARG types.
A strong and significant correlation (p < 0.05, ANOVA) was noted between genes
encoding resistance to tetracyclines and aminoglycosides (R = 0.77). Tetracycline resistance genes were significantly correlated with the abundance of Fermentiomonas caenicola
(R = 0.75); Proteiniclasticum ruminis (R = 0.73) and Methanosarcina thermophila (R = 0.75).
These correlations suggest that the above microorganisms could be potential carriers of
tetracycline resistance genes. A strong and significant correlation was found between the
abundance of Proteiniclasticum ruminis and Methanosarcina thermophila (R = 0.87). Strong
mutual correlations were also observed between the abundance of Erysipelothrix larvae
and Methanomassiliicoccales archaeon RumEnM2 (R = 0.78), and Methanothrix soehngenii and
Syntrophus aciditrophicus (R = 0.71). The presence of mutual correlations between microorganisms indicates that they cooperate and enter into syntrophic interactions during the AD
process [94], because hydrolysis, acidogenesis, and methanogenesis are the key phases of
the AD process, which involves a diverse group of microbial communities [95].
4. Conclusions
This study demonstrated that biomass supplementation with increasing concentrations
of AMO, ENRO and MET exerted a transient effect on CH4 production. The metagenomic
analysis revealed that prolonged mesophilic AD of cattle manure in the presence of all three
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tested antibiotics can modify the resistome profile and increase the relative abundance
of individual ARGs in digestates. However, there is also a risk of spreading ARGs in an
environment where genes can be transferred from the digestate to farmland, to surface
waters, to the soil, plant parts, and further down the food chain to livestock and humans.
The abundance of genes conferring resistance to tetracyclines, aminoglycosides and MLS
drugs increased significantly in digestate samples. The present findings indicate that at the
current level of technological development, ARGs are not removed during the AD process,
which can compromise the functions of soil-dwelling microorganisms in fields fertilized
with digestate. The above poses a direct health threat for humans as well as livestock that
consume fodder crops grown in digestate-fertilized fields. Therefore, effective strategies for
managing the AD process and the resulting digestates are needed to reduce the abundance
of ARGs in fermented biomass, and limit their further spread in the environment.
Supplementary Materials: The following Supplementary Materials can be downloaded at
https://www.mdpi.com/article/10.3390/en15051920/s1: Table S1: Methane (CH4 ) production
in samples from experimental bioreactors (I–VII) containing a mixture of amoxicillin (AMO), enrofloxacin (ENRO) and metronidazole (MET), and in samples from control bioreactors without
antibiotics (CS); Table S2: Dates and duration of seven experimental anaerobic digestion (AD) series;
Table S3: Correlations between microbial countsa and concentrations of antibiotic resistance genes
(ARGs).
Author Contributions: Conceptualization, I.W., M.C., M.H. and E.K.; methodology, M.H., E.F. and
P.R.; software, Ł.P. and J.P.J.; validation, I.W. and M.H.; investigation, I.W.; resources, M.H.; data
curation, Ł.P. and J.P.J.; writing—original draft preparation, I.W. and M.C.; writing—review and
editing, I.W., E.K. and M.H.; visualization, I.W. and Ł.P.; supervision, E.K.; project administration,
M.H.; funding acquisition, M.H. and I.W. All authors have read and agreed to the published version
of the manuscript.
Funding: This research was funded by the NATIONAL SCIENCE CENTER (Poland), grant number
No. 2016/23/B/NZ9/03669 and 2020/37/N/NZ9/00431. Moreover, the research was funded by the
Minister of Science and Higher Education under the “Regional Initiative of Excellence” program for
the years 2019–2022 (Project No. 010/RID2018/19, funding 12.000.000 PLN).
Institutional Review Board Statement: Not applicable.
Informed Consent Statement: Not applicable.
Data Availability Statement: A total of 21 metagenomic samples were submitted to the European
Nucleotide Archive (ENA) under accession No. PRJEB48924. The submitted data can be accessed at
https://www.ebi.ac.uk/ena/browser/view/PRJEB48924 (accessed on 3 March 2022).
Conflicts of Interest: The authors declare no conflict of interest. The funders had no role in the design
of the study; in the collection, analyses, or interpretation of data; in the writing of the manuscript, or
in the decision to publish the results.
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