- Research article
- Open Access
A long-term field experiment demonstrates the influence of tillage on the bacterial potential to produce soil structure-stabilizing agents such as exopolysaccharides and lipopolysaccharides
Environmental Microbiome volume 14, Article number: 1 (2019)
Stable soil aggregates are essential for optimal crop growth and preventing soil erosion. However, tillage is often used in agriculture to loosen the soil, which disrupts the integrity of these aggregates. Soil aggregation can be enhanced by bacteria through their ability to produce exopolysaccharides and lipopolysaccharides. These compounds stabilize soil aggregates by “gluing” soil particles together. However, it has yet to be shown how tillage influences the bacterial potential to produce aggregate-stabilizing agents. Therefore, we sampled conventional and reduced tillage treatments at 0–10 cm, 10–20 cm and 20–50 cm from a long-term field trial in Frick, Switzerland. We compared the stable aggregate fraction of the soil and the bacterial potential to produce exopolysaccharides (EPS) and lipopolysaccharides (LPS) under different tillage regimes by employing a shotgun metagenomic approach. We established a method which combines hidden Markov model searches with blasts against sequences derived from the Kyoto Encyclopedia of Genes and Genomes database to analyze genes specific for the biosynthesis of these compounds.
Our data revealed that the stable aggregate fraction as well as the bacterial potential to produce EPS and LPS were comparable under both tillage regimes. The highest potential to produce these compounds was found in the upper soil layer, which was disturbed by tillage, but had higher content of organic carbon compared to the layer below the tillage horizon. Additionally, key players of EPS and LPS production differed at different sampling depths. Some families with high potential to produce EPS and LPS, such as Chitinophagaceae and Bradyrhizobiaceae, were more abundant in the upper soil layers, while others, e.g. Nitrospiraceae and Planctomycetaceae, preferred the lowest sampled soil depth. Each family had the potential to form a limited number of different aggregate-stabilizing agents.
Our results indicate that conventional tillage and reduced tillage equally promote the bacterial potential to produce EPS and LPS in the tillage horizon. However, as major bacterial groups triggering EPS and LPS formation were not the same, it is likely that gene expression pattern differ in the different treatments due to various pathways of gene induction and transcription in different bacterial species.
Globally, 33% of land resources have been classified as moderately to highly degraded . The main causes of soil degradation are poor agricultural management practices, such as conventional tillage (CT), which lead to erosion, loss of soil organic carbon and nutrient imbalance . It turns out that a combination of reduced tillage (RT) and organic farming (OF) is a good compromise to diminish the aforementioned problems [3,4,5]. However, RT is still not commonly used by organic farmers due to increased weed pressure, topsoil compaction and restricted N availability, which may compromise yield [6, 7]. As even one-time ploughing may counteract the benefits of RT, these practices need to be developed further under long-term OF [8, 9].
One of the advantages of RT over CT practices is the better preservation of soil aggregates [10, 11]. The presence of stable aggregates defines good soil structure, which improves crop growth and prevents erosion [12, 13]. The stability of aggregates strongly depends on their size. Microaggregates (< 250 μm) form slower than macroaggregates (> 250 μm), but they are also more stable, even under unfavorable soil management systems [14, 15]. Aggregate formation results from complex interactions between soil fauna, microorganisms, roots, inorganic binding agents and different environmental variables. Fungi have been considered as the most important microorganisms involved in the formation of macroaggregates due to their hyphal structure [15, 16]. In contrast, bacteria are of higher importance for soil aggregation at the microscale, as they are capable of synthesizing exopolysaccharides (EPS) and lipopolysaccharides (LPS), which act as “glue” for soil particles [15, 16]. Bacteria use these compounds for cell attachment to mineral surfaces, which fosters the formation of composite building units and microaggregates [15,16,17]. While EPS are a very diverse group of high-molecular-weight polymers composed of sugar residues, LPS share a common structure. The number of possible EPS structures is almost infinite . Most EPS are initially synthesized intracellularly and then secreted to the external environment, which requires the contribution of at least three gene families: I) genes encoding for enzymes involved in biosynthesis of nucleotide sugars, II) genes encoding for glycosyltransferases, which catalyze transfer of the nucleotide sugars from activated donor molecules to specific acceptors in the plasma membrane, and III) genes encoding for proteins involved in EPS assembly and export . Alternatively, EPS can be synthesized extracellularly by different synthase proteins . Most enzymes involved in the EPS biosynthesis are strain-specific and can catalyze multiple metabolic processes.
LPS are glycolipids that are comprised of a lipid moiety (lipid A) and a polysaccharide (composed of O-antigen, outer core and inner core), both with variable structures . These parts are synthesized independently inside a cell, and then ligated together at the inner membrane, forming a mature LPS. The mature molecule is transported to the cell surface by several proteins that form an LPS export complex. As in EPS biosynthesis, very few of these proteins are conserved and catalyze LPS production only .
The gluing properties of both types of polysaccharides could be crucial in agricultural soils, as it was demonstrated that even slight changes in the sugar composition drastically changed the physical properties of the polysaccharide . Consequently, tillage might not only change the bacterial community composition in soil , but also the composition of EPS/LPS, and thus affect aggregate stability and de novo formation after disturbance.
The synthesis of EPS and LPS requires both high levels of energy and easily accessible carbon. Especially under CT, reduced soil organic carbon stocks have been frequently observed [4, 23, 24]. Therefore, we hypothesized that under long-term CT, abundance of EPS and LPS forming bacteria would be reduced compared to RT. To investigate this, high-throughput shotgun sequencing was used to obtain metagenomic information on microbiomes of three soil layers (0–10 cm, 10–20 cm and 20–50 cm) under RT and CT management from a long-term organic field trial in Frick (Switzerland). To analyze genes specific for EPS and LPS production, we used an approach which combined hidden Markov model (HMM) searches with blasts against sequences derived from the Kyoto Encyclopedia of Genes and Genomes (KEGG) database. As we investigated bacterial potentials samples were taken in spring where an influence of plants and fertilization could be excluded.
Materials and methods
Site description and soil sampling
Soil samples were taken from a long-term trial in Frick, Switzerland (47°30′N, 8°01′E, 350 m a.s.l.), established in 2002 by the Research Institute of Organic Agriculture (FiBL). The site was under conventional management until 1995, when it changed to organic standards in accordance with the European Union Regulation (EEC) No. 2092/91. The mean annual precipitation and temperature are 1000 mm and 8.9 °C, respectively. The soil is a Stagnic Eutric Cambisol with a pH of 7.1 and composed of 22% sand, 33% silt and 45% clay. The factorial design includes the factors tillage, fertilisation and biodynamic preparations and has been described in detail by Berner et al. .
In this study, only the two tillage treatments were compared: conventional tillage (CT) with a mouldboard plough operating at 15–18 cm depth, and reduced tillage (RT) with a chisel and a skim plough (5–10 cm) used to loosen the soil. In both systems, seedbed preparation was performed with a rotary harrow running at a depth of 5 cm. The usage of standard farming equipment was made possible by the plot size (12 m × 12 m). The plots were arranged in a strip-split-plot design.
Samples were taken from three out of four replicated plots per tillage system in the slurry fertilized plots without biodynamic preparations in March 2015 in a green manure ley, before tillage and subsequent maize cropping started. In 2014, winter wheat was harvested in July, followed by the seeding of a green manure mixture (Orgamix DS, Trifolium incarnatum, Vicia villosa, Avena sativa) in August, which was harvested in April 2015. All plots were fertilized with slurry during the wheat growing season in 2014 (the exact dates and fertilization details are summarized in Additional file 1). Soil samples were taken using a soil auger with a diameter of 2.5 cm. Approximately 10 cores per plot were sampled to a soil depth of 50 cm. Each soil core was divided into three layers: 0–10 cm, 10–20 cm and 20–50 cm. Samples from the same layer of each plot were homogenized, resulting in 18 samples (3 depths × 2 tillage treatments × 3 plot replicates). The samples were directly cooled in the field and either processed immediately (biochemical analyses) or stored in − 20 °C until processing (DNA extraction and sequencing).
Physical, chemical and major biological properties of soils
We determined the stable aggregate fraction (SAF) of the soils by a wet sieving technique, where 5 g of moist soil was immersed in water using a sieving apparatus according to Murer et al. . After 5 min of moving the sieves up and down in the water phase, the remainder on the sieve consisting of aggregates and particles > 0.25 mm was dried at 105 °C. The aggregates were then destroyed by adding a 0.1 M Na4P2O7 solution, leaving only particles > 0.25 mm (sand and organic debris) on the sieve that were dried again. Apart from using moist soil without further fractionation, the method follows the details as given by Murer et al. .
Soil organic carbon (SOC) concentration was determined by wet oxidation of 1 g of air-dried and ground soil in 20 ml of concentrated H2SO4 and 25 ml of 2 M K2Cr2O7. The determination of dissolved organic carbon (DOC) and microbial biomass carbon (Cmic) was accomplished by means of a chloroform fumigation extraction method (CFE) using 20 g of moist soil, sieved on a 5 mm sieve. 0.5 M K2SO4 solution was added at a weight to volume (w/v) ratio of 1:4. Subsequently, measurements were performed using a TOC/TNb analyzer (Analytik Jena AG, Germany). DOC was determined from the non-fumigated samples, and Cmic was calculated as a difference between the fumigated and the non-fumigated samples. The assessment of SOC and Cmic was described in detail by Krauss et al. .
DNA extraction and sequencing
Total nucleic acids were directly extracted from 0.5 g of frozen soil according to the phenol-chloroform based DNA/RNA coextraction protocol described by Lueders et al. . Beat beating was performed by means of CKMix tubes and a Precellys24 homogenizer (Bertin Technologies, France). Extracted DNA was checked for purity using a NanoDrop 1000 spectrophotometer (Thermo Fisher Scientific, USA). The quantity was also verified by means of a Quant-iT PicoGreen dsDNA Assay Kit (Life Technologies, USA). Extracted DNA was then stored in − 20 °C until further processing.
One microgram of DNA from each sample was sheared using an E220 Focused-ultrasonicator (Covaris, USA), following the manufacturer’s guideline for the target size of 500 bp (conditions: peak incident power – 175 W, duty factor – 5%, cycles per burst – 200, treatment time – 35 s, temperature – 7 °C, water level – 6, sample volume – 50 μl, intensifier – yes). Libraries were prepared with 50–100 ng of the sheared DNA, using a NEBNext Ultra DNA Library Prep Kit for Illumina, and NEBNext Multiplex Oligos for Illumina (New England Biolabs, UK) as barcodes. According to the manufacturer’s manual, the NEBNext Adaptor from Illumina was diluted 10-fold to prevent the occurrence of dimers. Size selection was performed with Agencourt AMPure XP beads (Beckman Coulter, USA), using the volumes selecting for libraries with 400–500 bp inserts. The AMPure XP beads were also used for cleanup of PCR amplification and a following additional cleanup step to eliminate the residual primer dimers (1:0.6 DNA to bead ratio).
Library size was estimated using High Sensitivity DNA Analysis Kits together with a 2100 Bioanalyzer (Agilent, USA). DNA concentration was subsequently assessed by means of a Quant-iT PicoGreen dsDNA Assay Kit. Libraries were then diluted to a concentration of 4 nM each and pooled equimolar. 10 pM of the mixture was spiked with 30% PhiX, used as a quality and calibration control , and sequenced on a MiSeq sequencer using a MiSeq Reagent Kit v3 for 600 cycle (Illumina, USA).
Data filtering and taxonomic analysis
Raw sequencing data attained from the MiSeq was filtered according to Vestergaard et al.  by removing remnant adaptor sequences and trimming the reads. This was accomplished by using AdapterRemoval  set to: 5′/3′ terminal minimum Phred quality = 15, minimum read length = 50. PhiX contamination was removed using DeconSeq . For taxonomic annotation, filtered reads were blasted against the National Center for Biotechnology Information Non-Redundant (NCBI-NR) protein sequences database (October 2015) using Diamond (version 0.5.2.32) with sensitive parameters . Based on the top 25 blast results (i.e. hits with the lowest e-value), a unique taxon ID was assigned to each filtered read with the MEtaGenome Analyzer software (MEGAN, version 5.10.6) . During the MEGAN analysis, the following parameters were applied: MinScore = 50.0, MaxExpected = 0.01, TopPercent = 10.0, MinSupport = 1, MinComplexity = 0. Additionally, 16S rRNA gene sequences were identified using SortMeRNA (version 2.0) . Taxonomy was assigned to those reads using QIIME (version 1.9.1)  based on the SILVA database (release 123).
Protein sequences associated with EPS and LPS biosynthesis and excretion were downloaded directly from the online Kyoto Encyclopedia of Genes and Genomes (KEGG) Orthology database (October 2016). They were examined for the presence of function-specific conserved domains using CD-search . KEGG Orthology (KO) entries which contained such domains were then used to construct specific databases by means of Diamond. Hidden Markov models (HMMs) of corresponding conserved domains were obtained from the TIGRFAMs database (version 15)  and the Pfam database (version 30) . FragGeneScan (version 1.19)  was used on the filtered sequencing reads to predict open-reading frames, which were subsequently scanned with HMMER (version 3) (hmmer.org). Reads matching the downloaded HMMs (E-value threshold = 10− 5), were blasted against the self-built KO databases. A KO ID was assigned to those reads for which the top 25 blast results were consistent. The specificity of this approach was verified by using blastx against the Non-redundant protein sequences (nr) database. Out of 81 examined KO numbers (67 for EPS and 14 for LPS), 14 gave sufficiently specific results. The results were considered sufficiently specific if 25 randomly selected reads (or all if less reads were assigned) per a KO number were assigned to the function of interest. Analysis of EPS and LPS biosynthesis and excretion was performed using separate databases. Open-reading frames of the assigned reads were searched against the full Pfam and TIGRFAMs databases. This resulted in 81.8% of the reads matching the downloaded HMMs. All examined KO numbers are listed in Additional file 2 and the HMMs and KO numbers used for the analysis are summarized in Table 1.
Statistical analysis and data visualization
All statistical analyses were conducted using R version 3 . Metagenomic datasets were analyzed based on relative abundances of reads. These were obtained by dividing the number of reads assigned to a gene or organism by the total number of filtered reads per sample, and multiplying by 100. Effects of tillage, depth and their possible interaction were detected by multilevel models. For this purpose, the lme function from the nlme package was used . The influence was considered significant when the p-value was below 5% (P < 0.05). Differences between sampled depths were identified by setting the following contrasts: 0–20 cm vs 20–50 cm and 0–10 cm vs 10–20 cm. For data derived from the metagenomic datasets, the Benjamini-Hochberg procedure was performed prior to analyzing contrasts. The Shannon-Wiener index was calculated using the alpha.div function of the R asbio package to measure diversity within the samples . To visualize the level of dissimilarity between the samples, non-metric multidimensional scaling (NMDS) ordination plots were created based on the Bray-Curtis distance metrics, using the metaMDS function in the R vegan package . The core microbiomes were identified by means of InteractiVenn . For the purpose of calculating these cores, a family was recognized as present in a treatment only if it was detected in at least two out of three replicates.
The stable aggregate fraction (SAF) of the soil, soil organic carbon (SOC), dissolved organic carbon (DOC) and microbial biomass carbon (Cmic) data is summarized in Table 2. Aggregate stability was highest in the 20–50 cm depth, and did not differ significantly between the upper depths. It was also not significantly influenced by tillage. SOC stocks decreased with depth, and were higher in the 0–20 cm depth under RT compared to CT. DOC concentrations were highest in the 0–10 cm depth under RT, and showed little difference between the other samples. Microbial biomass decreased with depth, and was more stratified under RT. In the 0–10 cm depth, Cmic values were higher under RT.
Shotgun sequencing characteristics
Shotgun sequencing of the 18 libraries, prepared from two tillage treatments – conventional (CT) and reduced (RT) – sampled at three depths (0–10 cm, 10–20 cm and 20–50 cm) from three independent plots treated as replicates, generated 11.8 gigabases of data in total. This corresponded to 39.307.875 filtered reads with an average length after trimming of 297 bp. Details of the sequencing run are summarized in Additional file 3.
Taxonomic analysis of the general bacterial community
When all filtered reads were blasted against the NCBI-NR database, 55.8% were assigned to Bacteria, 1.2% to Archaea, 1.3% to Fungi and 41.7% to others. Further analysis focused on bacteria and was conducted at the level of family, at which 21.1% of filtered reads were assigned. In total, bacteria comprised 296 families.
The non-metric multidimensional scaling (NMDS) ordination plot (Additional file 4A) showed a difference between the composition of bacterial families originating from the deepest sampled soil layer (20–50 cm) and the upper soil layers (0–10 cm and 10–20 cm), but revealed no clear separation of the tillage treatments. This was confirmed by means of a multilevel model. Abundances of 103 families were influenced by depth, while none was affected by tillage, and one by the interaction of both factors. The full list of impacted families can be taken from Additional file 5.
In-depth analysis of the effects of tillage, depth and their interaction on the general community structure was performed on dominant families whose abundance exceeded 0.5% (Fig. 1a). The most abundant family, Anaerolineaceae, together with Nitrospiraceae, were found mainly in 20–50 cm. Chitinophagaceae, Bradyrhizobiaceae, Polyangiaceae and Cytophagaceae had higher abundance in 0–20 cm. Planctomycetaceae, Acidobacteriaceae, Verrucomicrobia subdivision 3, Flavobacteriaceae and Solibacteraceae were not significantly influenced by either depth or tillage.
The results from the taxonomic analysis encompassing the entire metagenomic datasets were supported by SILVA’s taxonomic annotations of the 16S rRNA gene. Of all filtered reads, 0.21% were assigned to the 16S rRNA gene. With both approaches, the bacterial communities showed similar distribution patterns and one third of the dominant families remained the same, with Anaerolineaceae staying the most abundant, regardless of the assignment method used (Additional file 6).
Relative abundances of genes catalyzing EPS and LPS synthesis and excretion
An approach combining hidden Markov model (HMM) searches with blasts against sequences derived from the Kyoto Encyclopedia of Genes and Genomes (KEGG) database was used to target genes specific for the biosynthesis and excretion of alginate, colanic acid, levan and other EPS, as well as LPS (Table 1). Sufficient coverage of the diversity of the analyzed genes was confirmed by performing explanatory rarefaction analysis (Additional file 7).
In total, the investigated genes comprised 0.018% of all filtered reads (Fig. 2). Dominant genes, with a relative abundance above 0.005% of total reads, were wza, lptF and lptG, which encode for an outer membrane protein responsible for EPS excretion, and permeases of the LptBFGC LPS export system, respectively. Moderately abundant genes (> 0.001%) were wcaB, wcaF (encoding for a colanic acid biosynthesis acetyltransferases) and wzt (a gene which encodes for an ATP-binding protein of the LPS O-antigen transport system). Genes algE, algJ, wcaK/amsJ, epsA, epsG, sacB and lptC were the least abundant, with just a few reads annotated. Multilevel model analysis revealed depth as the main factor affecting the distribution pattern of the investigated genes. Specifically, the relative abundance of wcaF and lptFG decreased with depth by half. In addition, the epsA gene (encoding for an EPS biosynthesis tyrosine kinase modulator) was influenced by interaction of depth and tillage. This gene was more abundant in 0–10 cm under RT, compared to 20–50 cm under CT, and no reads were detected in 10–20 cm under both CT and RT. The majority of the analyzed genes, namely wza, algEJ, wcaB, wcaK/amsJ, kpsE, epsG, sacB, wzt and lptC, were not significantly affected by either tillage or depth.
Investigation of potential EPS/LPS producers
One hundred thirty-eight bacterial families harbored the investigated genes, including all dominant families (Fig. 1b). The highest numbers of sequences related to EPS and LPS synthesis and excretion (> 0.001%) were assigned to Chitinophagaceae, Nitrospiraceae and Planctomycetaceae. Anaerolineaceae, despite their high abundance, harbored a very low number of copies of the investigated genes (< 0.0002%).
The NMDS (Additional file 4B) plot once again revealed depth as the main factor affecting the distribution of the investigated genes among bacterial families. However, the influence of depth was much less pronounced than in case of the general bacterial community (Additional file 4A). This was confirmed with a multilevel model. The overall relative abundances of the investigated genes were impacted by depth in four families affiliated with EPS/LPS synthesis and excretion, while tillage had no influence, and interaction had an effect on one family only. The full list of influenced families can be taken from Additional file 5.
Taxonomic affiliation of the individual genes encoding for proteins involved in EPS and LPS biosynthesis was analyzed using a heatmap (Fig. 3). The most abundant genes, wza and lptFG, were harbored by most of the dominant families. Anaerolineaceae had neither wza nor lptFG, but harbored the wzt gene, which is part of the same LPS synthesis pathway. Moreover, Polyangiaceae carried the wza gene, but showed no potential to produce LPS. The other investigated genes were not so widely distributed among the dominant families. In particular, algE, epsA and sacB, encoding respectively for alginate export outer membrane protein, exopolysaccharide biosynthesis tyrosine kinase modulator and levansucrase, were not detected in any of the dominant families. As shown by means of a multilevel model, the gene copy numbers of wcaF, epsA, sacB, wzt and lptC were influenced by interaction of tillage and depth in Chitinophagaceae, Bacillaceae, Micrococcaceae, Candidatus Brocadiaceae and Sulfuricellaceae, whilst the abundances of algJ and lptC changed with depth in Polyangiaceae and Sphingomonadaceae, respectively.
Since wza and lptFG were dominating among the investigated genes, their taxonomic affiliation was analyzed in more detail. These genes were present in a total of 50 families associated with 11 phyla. The core microbiomes harboring the respective genes under both tillage treatments were identified at each sampled depth (Fig. 4). At each depth, on average ten families carried the respective genes under both tillage managements, while five were unique for either CT or RT. Overall, the three genes harbored by the core families accounted for 22.7% of all reads assigned to all the investigated genes, while 1.8 and 2.1% were unique for CT and RT, respectively. The diversity of families carrying wza and lptG significantly decreased with depth (Additional file 8). Depth triggered a decrease of wza and lptFG in Chitinophagaceae. The relative number of wza gene copies decreased with depth also in Flammeovirgaceae and Labilitrichaceae. Furthermore, depth caused a decrease of lptG in Bdellovibrionaceae, but lptF increased in Nitrospiraceae. Finally, the interaction of depth and tillage affected lptG in Pseudomonadaceae. This gene was more abundant in 0–10 cm under RT, compared to 20–50 cm under CT, and no reads were detected in the other samples.
Different factors could affect the stable aggregate fraction in soil
EPS and LPS are of great importance for agricultural soils, as they reduce soil erodibility by improving soil structure . However, tillage disrupts soil aggregates and alters soil physical and chemical properties. These include bulk density, pore structure, water availability and soil organic carbon . Thus, changes in bacterial communities are likely to occur. This has been reported by multiple studies [46,47,48,49,50]. Especially CT disturbs bacterial habitats and dilutes nutrient pools by mixing topsoil with subsoil. In our study, soil organic carbon (SOC), dissolved organic carbon (DOC) and microbial biomass carbon (Cmic) had higher values in the tillage horizon under RT compared to CT. This corresponds to the data found in the literature [23, 51,52,53]. The increase of Cmic suggests that the absolute number of bacteria capable of synthesizing EPS and LPS should be higher under RT. Thus, we assumed that the higher DOC concentrations promotes bacteria which are able to produce EPS and LPS, and that the stable aggregate fraction (SAF) of the soil is higher under RT. Surprisingly, at our sampling site, SAF was comparable between the two tillage systems and increased significantly only below the tillage horizon. However, this might be caused by soil physical properties. Specifically, the clay content (45%) was very high at our site. Meta-analysis performed by Cooper et al.  suggests that the differences between tillage systems could be more pronounced in soils with a lower clay content (< 40%). Building good soil structure is more challenging in light, sandy soils, as they lack the fine particles necessary to form stable soil aggregates . Conversely, soil biology has a strong influence on SAF. This includes the activity of bacteria, fungi, earthworms and plants. On one hand, the effect of plants and earthworms is rather indirect and includes for example cast formation by earthworms or increasing microbial activity by the release of organic substances to the soil via the rhizosphere of plants [15, 16]. On the other hand, bacteria and fungi directly promote aggregate formation by the excretion of gluing agents such as EPS, LPS and fungal glycoproteins, or by physical binding of soil particles by fungal mycelium . Similar to the general increase of Cmic in the topsoil under RT, Kuntz et al.  also observed higher fungal abundances in that soil layer.
While it is obvious that ploughing physically disturbs fungal hyphae and consequently aggregates connected to them, the effect on the bacterial potential to promote aggregate formation can be much more subtle. Especially EPS composition and regulation of the respective genes is species-specific, thus a shift in the bacterial community strongly influences their potential to promote aggregate formation. To detect changes in the bacterial potential to produce EPS and LPS, we applied a metagenomic approach. As many proteins or their functional domains from genes encoding for EPS and LPS biosynthesis pathways are associated with other cellular activities as well , we used a pipeline combining hidden Markov model (HMM) searches with blasts against sequences derived from the Kyoto Encyclopedia of Genes and Genomes (KEGG) database to target selected genes specific for our functions of interest. Although the contribution of fungi to aggregate formation is well accepted, our analysis exclusively focused on bacteria due to the well-described biases of the existing databases towards bacteria . This is also visible in our dataset, where 55.8% of sequences were assigned to bacteria, while only 1.3% could be assigned to fungi. Moreover, fungal genes require long reads for accurate annotation due to many intronic sequences .
Key genes encoding for selected EPS and LPS biosynthesis pathways
Identified as key components of the analyzed EPS and LPS synthesis and excretion pathways were wza and lptFG, which encode for an outer membrane protein Wza and permeases of the LptBFGC LPS export complex (LptF and LptG), respectively. Wza acts as a translocation channel across the outer membrane for a variety of exopolysaccharides in a wide range of taxa. It is also characterized by the presence of a very well conserved polysaccharide export sequence domain (pfam 02563) . Similarly, LptF and LptG are essential for transport of mature LPS to the outer membrane. These two proteins are highly conserved among Gram-negative bacteria, unlike another component of the LptBFGC transport complex, LptC [59, 60]. Benedet et al.  recently reported the isolation of mutants lacking LptC and suggested its supportive role in the LPS translocation. In our study, the respective gene, lptC, had just a few reads annotated and was detected in only one of the dominant families, Nitrospiraceae, even though all of them belong to phyla known to produce LPS . The family Nitrospiraceae is essential for nitrification, and thus its high abundance in agricultural soils is expected .
Less abundant genes were wcaBF and wzt, encoding for the colanic acid biosynthesis acetyltransferases WcaB and WcaF, and an ATP-binding protein Wzt of the LPS O-antigen transport system, respectively. Relatively high abundances of the genes from the colanic acid biosynthesis pathway are not surprising, as colanic acid is one of the most common exopolysaccharides. However, it is also one of the exopolysaccharides secreted by Wza. Therefore, wcaBF were less abundant than wza due to their lower universality . In contrast, wzt is involved in translocating the O-antigen to the outer leaflet of the inner membrane where it gets ligated to the other parts of LPS . Thus, the lower abundance of wzt compared to lptFG can be explained by the fact that the O-antigen is not an essential component of LPS .
Finally, a very low number of reads was assigned to the other investigated genes, which catalyze the biosynthesis and export of alginate, colanic acid, levan and other extracellular and capsular polysaccharides. EPS biosynthesis pathways are generally poorly conserved and often species or strain-specific, so this result was expected [19, 20, 65]. Also the low abundances of algEJ, encoding for alginate export outer membrane protein AlgE and alginate biosynthesis acetyltransferase AlgJ, were understandable because alginate is produced by various bacteria from the genera Pseudomonas and Azotobacter . These genera belong to the family Pseudomonadaceae, which was not dominant in our metagenomes. Pseudomonadaceae contains many plant growth promoting endophytes and rhizobacteria . Its low abundance could be related to the poorly established vegetation at the time of sampling (March) and the fact that bulk soil samples were investigated instead of rhizosphere samples.
EPS and LPS biosynthesis is important in agricultural soils, yet could be easily hindered
In our metagenomes, almost half (46.6%) of all bacterial families harbored genes affiliated with EPS and LPS biosynthesis. These included all dominant families whose abundance exceeded 0.5%. The ability to form EPS or LPS seems to be, therefore, an important trait for bacteria living in agricultural soils.
Despite the fact that all families dominating in our metagenomes harbored genes encoding for EPS or LPS biosynthesis, none of them accommodated genes from more than one of the investigated EPS biosynthesis pathways. This is not surprising, as few bacteria are known to produce more than one type of EPS . Nonetheless, some of the analyzed genes were not represented in any of the dominant families. This could have several reasons, including: (i) that those genes might be harbored by low abundant families only, which were below the detection limit of our approach, or (ii) no genome of a representative taxon was sequenced so far. This is very likely, as databases for sequencing analysis are still biased towards fast-growing bacteria, while soil contains many slow-growing bacteria, which are difficult to isolate and culture.
Bacterial potential to produce EPS and LPS is affected by the interplay of tillage type and tillage depth
Tillage not only disrupts soil aggregates, but also alters soil physical and chemical properties. Especially CT disturbs microbial habitats and reduces available nutrients by mixing topsoil with subsoil. Since bacterial polysaccharides contribute to soil aggregation, which was reported to be lower under CT [10, 11], and EPS and LPS production requires a lot of carbon, we hypothesized that CT weakens the bacterial potential to produce soil structure-stabilizing agents. Contradictory to this hypothesis, but similar to the SAF results in our study, the tillage system influenced bacterial community composition and the potential to synthesize EPS and LPS only in the context of the depth factor. Direct effects of tillage were visible only when closely analyzing the taxonomic affiliation of the key genes of the investigated EPS and LPS biosynthesis pathways (wza, lptFG). At each soil depth, unique families harboring the respective genes under either CT or RT were described. These findings are in accordance with the theory about functional redundancy, which states that different taxa are able to perform the same functions under changed conditions . However, EPS and LPS produced by different bacteria may differ in quality, and can have different gluing properties [70, 71]. Therefore, the differences in aggregate preservation observed in other studies could be related to the differences in the properties of EPS and LPS produced under CT and RT.
The fact that the differences between tillage systems at our sampling sites were not more pronounced in comparison to other studies, is surprising, but not unprecedented. In fact, our results are in agreement with other functional analyses of agricultural soils. The work of de Vries et al. , who also compared CT and RT using metagenomics, and Grafe et al. , who compared different fertilization regimes, found little significant effects on bacterial community structure and functionality. Both studies implied that under long-term management, bacterial communities are very stable and hardly differ between treatments. In fact, it is more likely that regulation takes place on the RNA level, as tillage alters soil conditions, and thus might influence metabolic activity of soil structure-stabilizing bacteria. Ultimately, the yield of EPS and LPS could be increased or decreased by multiple factors, e.g. carbon sources or oxygen availability . Thus, a metatranscriptomic analysis of the soil samples should be the next step. Ideally, omics data and SAF measurements should be correlated with the content of bacterial polysaccharides in soil. Redmile-Gordon et al.  made efforts to evaluate the suitability of different extracellular polymeric substances extraction methods for this medium. However, the existing methodologies are still biased and do not allow for distinction between polysaccharides of different origins (bacterial, fungal, plant, etc.). Therefore, further research needs to address these issues in order to establish a standardized protocol.
RT and CT promote the potential to produce EPS and LPS in bacteria
To our knowledge, previous metagenomic comparisons of tillage systems encompassed only surface soil samples [46,47,48,49,50]. However, other studies on tillage included analyses of chemical and physical properties of soil also at deeper levels [74,75,76]. The studies revealed that tillage can differentially impact bacterial habitats of different soil layers. Gadermaier et al.  demonstrated, that also at our sampling site the effects of tillage on soil organic carbon, microbial biomass and soil nutrients, varied with the depth of sampling. Therefore, we expected that bacterial communities at different depths would be differently affected by tillage, prompting the inclusion of a depth factor in our metagenomic analysis.
It is well-known that bacterial communities change with depth in undisturbed soils [77,78,79]. We showed that the composition of bacterial families in the upper soil depths (in the tillage horizon) differs from the one in lower soil depths (below the tillage horizon) also in tilled soils. This happens because specific conditions of different soil depths select for the best-adapted microorganisms. That is to say, deeper soil layers are generally more oxygen-depleted and nutrient-poor than upper soil layers. In the deepest soil layer which we sampled, the dominant family was Anaerolineaceae. Unsurprisingly, its members are strictly anaerobic oligotrophs [80, 81]. Including Anaerolineaceae, 34.8% of bacterial families detected in our metagenomes were significantly influenced by depth. Furthermore, we showed that in tilled soils, depth has not only a big influence on bacterial community composition, but also on relative abundances of genes involved in EPS and LPS synthesis and excretion. The relative abundances of wza, wcaF and lptFG were higher in the upper soil layers. Additionally, epsA was influenced by the interaction of tillage and depth, but its low abundance undermines the significance of this finding. Moreover, the diversity of bacterial families which harbored wza and lptG, two out of three most abundant genes of the analyzed biosynthesis pathways, decreased with depth. These effects should be even more pronounced due to the stratification of Cmic, which was significantly higher under both CT and RT, in the 0–20 cm layers as opposed to the 20–50 cm layers. Although we expected higher potential to produce EPS and LPS in the deeper, undisturbed soil layers, these observations suggest that EPS and LPS synthesis plays a bigger role in the surface soil layers, which are regularly disturbed by tillage. This could be explained by better aeration and availability of nutrients in the tillage horizon, as these parameters are known to be important for EPS and LPS production [18, 82, 83]. Otherwise, Galant et al.  postulated that disturbances increase the diversity and productivity of bacteria performing important ecological functions, which also coincides with our results. In our study, the disturbance caused by tillage could select for bacteria which are capable of synthesizing protective compounds, such as EPS and LPS.
Finally, it is difficult to separate depth and tillage effects, as the depth effects might be also induced by tillage. The stratification of soil chemical and physical properties in our study was artificially induced by tillage . In particular, soil organic carbon (SOC) steadily decreased with depth under both CT and RT. By introducing such changes in soil properties along the soil profile, tillage indirectly caused the shifts in bacterial communities allocated as the effects of depth. Those shifts could be driven primarily by the disturbance caused by tillage. Specifically, tillage could stir the established bacterial communities in the tillage horizon, making it possible for new taxa to emerge. At the same time, a long-term competition in the undisturbed soil layers below the tillage horizon would enable only the best-adapted bacteria to thrive. This type of competition-driven dominance of selected taxa is well-known in ecological communities [85, 86]. Moreover, it has recently been demonstrated that periodic disturbances have an impact on bacterial communities by promoting the cohabitation of ecologically different bacteria . In conclusion, as similar effects of depth were detected under both CT and RT, the impact of tillage in general, might be more selective than the subtle differences between these two systems.
Although a typical stratification of soil carbon and microbial biomass was observed under RT in our study, no difference in the stable aggregate fraction of the soil or the potential to produce EPS and LPS was observed between RT and CT systems. While the potential to produce EPS and LPS was enhanced in the tillage horizon, tillage affected the taxonomic affiliation of genes encoding for proteins involved in the biosynthesis of specific EPS and LPS. These compounds can have different properties depending on the bacterial producers. Thus, the regulation of EPS and LPS formation can take place at two levels: (i) even small changes in the bacterial community composition could disturb the overall capacity of EPS and LPS to stabilize soil structure, or (ii) regulation takes place on the level of gene expression. Consequently, future studies need to figure out under which conditions the potential to produce EPS and LPS is recalled. However, the fast turnover of mRNA would require another sampling strategy which accounts for that dynamic, such as high resolved samplings throughout the season and the day, as beside tillage, also carbon input by plants and fertilization might influence expression of the respective genes. Moreover, soil at the sampling site was already well-structured due to its high clay content. We expect a stronger effect of tillage in sandy soils, which lack the fine particles necessary to form stable soil aggregates.
Microbial biomass carbon
Dissolved organic carbon
Stable aggregate fraction
Soil organic carbon
FAO, ITPS. Status of the world’s soil resources (SWSR) – main report. Rome: Food and Agriculture Organization of the United Nations and Intergovernmental Technical Panel on Soils; 2015.
Montgomery DR. Soil erosion and agricultural sustainability. P Natl Acad Sci USA. 2007;104:13268–72.
Berner A, Hildermann I, Fliessbach A, Pfiffner L, Niggli U, Mäder P. Crop yield and soil fertility response to reduced tillage under organic management. Soil Till Res. 2008;101:89–96.
Gadermaier F, Berner A, Fließbach A, Friedel JK, Mäder P. Impact of reduced tillage on soil organic carbon and nutrient budgets under organic farming. Renew Agr Food Syst. 2012;27:68–80.
Mäder P, Fliessbach A, Dubois D, Gunst L, Fried P, Niggli U. Soil fertility and biodiversity in organic farming. Science. 2002;296:1694–7.
Peigné J, Ball BC, Roger-Estrade J, David C. Is conservation tillage suitable for organic farming? A review. Soil Use Manage. 2007;23:129–44.
Cooper J, Baranski M, Stewart G, Nobel-de Lange M, Bàrberi P, Fließbach A, Peigné J, Berner A, Brock C, Casagrande M. Shallow non-inversion tillage in organic farming maintains crop yields and increases soil C stocks: a meta-analysis. Agron Sustain Dev. 2016;36:1–20.
Grandy AS, Robertson GP, Thelen KD. Do productivity and environmental trade-offs justify periodically cultivating no-till cropping systems? Agron J. 2006;98:1377–83.
Stockfisch N, Forstreuter T, Ehlers W. Ploughing effects on soil organic matter after twenty years of conservation tillage in Lower Saxony, Germany. Soil Tillage Res. 1999;52:91–101.
Bartlova J, Badalikova B, Pospíšilová L, Pokorný E, Šarapatka B. Water stability of soil aggregates in different systems of tillage. Soil Water Res. 2015;10:147–54.
Singh P, Heikkinen J, Mitra S, Regina K. Impact of tillage and residue management practices on soil aggregates and soil organic carbon. In: Raju NJ, editor. Geostatistical and geospatial approaches for the characterization of natural resources in the environment. Cham: Springer; 2016. p. 381–4.
Horn R, Taubner H, Wuttke M, Baumgartl T. Soil physical properties related to soil structure. Soil Till Res. 1994;30:187–216.
Lynch JM, Bragg E. Microorganisms and soil aggregate stability. In: Stewart BA, editor. Advances in soil science. New York: Springer; 1985. p. 133–71.
Snyder VA, A VM. Structure. In: Daniel H, editor. Encyclopedia of soils in the environment. Volume 4. New York: Academic Press; 2005. p. 54–68.
Totsche KU, Amelung W, Gerzabek MH, Guggenberger G, Klumpp E, Knief C, Lehndorff E, Mikutta R, Peth S, Prechtel A. Microaggregates in soils. J Plant Nutr Soil Sc. 2018;181:104–36.
Six J, Bossuyt H, Degryze S, Denef K. A history of research on the link between (micro) aggregates, soil biota, and soil organic matter dynamics. Soil Till Res. 2004;79:7–31.
Abu-Lail NI, Camesano TA. Role of lipopolysaccharides in the adhesion, retention, and transport of Escherichia coli JM109. Environ Sci Technol. 2003;37:2173–83.
Suresh Kumar A, Mody K, Jha B. Bacterial exopolysaccharides–a perception. J Basic Microb. 2007;47:103–17.
Schmid J, Sieber V, Rehm B. Bacterial exopolysaccharides: biosynthesis pathways and engineering strategies. Front Microbiol. 2015;6:496.
Pereira SB, Mota R, Santos CL, De Philippis R, Tamagnini P. Assembly and export of extracellular polymeric substances (EPS) in cyanobacteria: a phylogenomic approach. Adv Bot Res. 2013;65:235–79.
Hunt F. Patterns of LPS synthesis in gram negative bacteria. J Theor Biol. 1985;115:213–9.
Wang X, Quinn PJ. Lipopolysaccharide: biosynthetic pathway and structure modification. Prog Lipid Res. 2010;49:97–107.
Krauss M, Ruser R, Müller T, Hansen S, Mäder P, Gattinger A. Impact of reduced tillage on greenhouse gas emissions and soil carbon stocks in an organic grass-clover ley-winter wheat cropping sequence. Agric Ecosyst Environ. 2017;239:324–33.
Quintero M, Comerford NB. Effects of conservation tillage on total and aggregated soil organic carbon in the Andes. Open J Soil Sci. 2013;3:361–73.
Murer EJ, Baumgarten A, Eder G, Gerzabek MH, Kandeler E, Rampazzo N. An improved sieving machine for estimation of soil aggregate stability (SAS). In: Brussaard L, Kooistra MJ, editors. Soil Structure/Soil Biota Interrelationships. Amsterdam: Elsevier; 1993. p. 539–47.
Lueders T, Manefield M, Friedrich MW. Enhanced sensitivity of DNA-and rRNA-based stable isotope probing by fractionation and quantitative analysis of isopycnic centrifugation gradients. Environ Microbiol. 2004;6:73–8.
Mukherjee S, Huntemann M, Ivanova N, Kyrpides NC, Pati A. Large-scale contamination of microbial isolate genomes by Illumina PhiX control. Stand Genomic Sci. 2015;10:18.
Vestergaard G, Schulz S, Schöler A, Schloter M. Making big data smart—how to use metagenomics to understand soil quality. Biol Fert Soils. 2017;53:479–84.
Schubert M, Lindgreen S, Orlando L. AdapterRemoval v2: rapid adapter trimming, identification, and read merging. BMC Res Notes. 2016;9:88.
Schmieder R, Edwards R. Fast identification and removal of sequence contamination from genomic and metagenomic datasets. PLoS One. 2011;6:e17288.
Buchfink B, Xie C, Huson DH. Fast and sensitive protein alignment using DIAMOND. Nat Methods. 2015;12:59–60.
Huson DH, Mitra S, Ruscheweyh H-J, Weber N, Schuster SC. Integrative analysis of environmental sequences using MEGAN4. Genome Res. 2011;21:1552–60.
Kopylova E, Noé L, Touzet H. SortMeRNA: fast and accurate filtering of ribosomal RNAs in metatranscriptomic data. Bioinformatics. 2012;28:3211–7.
Caporaso JG, Kuczynski J, Stombaugh J, Bittinger K, Bushman FD, Costello EK, Fierer N, Pena AG, Goodrich JK, Gordon JI. QIIME allows analysis of high-throughput community sequencing data. Nat Methods. 2010;7:335–6.
Marchler-Bauer A, Derbyshire MK, Gonzales NR, Lu S, Chitsaz F, Geer LY, Geer RC, He J, Gwadz M, Hurwitz DI. CDD: NCBI's conserved domain database. Nucleic Acids Res. 2015;43:D222–6.
Haft DH, Selengut JD, Richter RA, Harkins D, Basu MK, Beck E. TIGRFAMs and genome properties in 2013. Nucleic Acids Res. 2013;41:D387–95.
Finn RD, Coggill P, Eberhardt RY, Eddy SR, Mistry J, Mitchell AL, Potter SC, Punta M, Qureshi M, Sangrador-Vegas A. The Pfam protein families database: towards a more sustainable future. Nucleic Acids Res. 2016;44:D279–85.
Rho M, Tang H, Ye Y. FragGeneScan: predicting genes in short and error-prone reads. Nucleic Acids Res. 2010;38:e191.
R Core Team. R: a language and environment for statistical computing. Vienna: R Foundation for Statistical Computing; 2016.
Pinheiro J, Bates D, DebRoy S, Sarkar D. nlme: Linear and nonlinear mixed effects models. 2018; R package version 3.1–131.1.
Aho K. asbio: a collection of statistical tools for biologists. 2015; R package version 1.1–5.
Oksanen J, Blanchet FG, Kindt R, Legendre P, Minchin PR, O'Hara RB, Simpson GL, Solymos P, Steven MHH, Wagner H. vegan: community ecology package. 2015; R package version 2.3–0.
Heberle H, Meirelles GV, da Silva FR, Telles GP, Minghim R. InteractiVenn: a web-based tool for the analysis of sets through Venn diagrams. BMC Bioinformatics. 2015;16:169.
Barthes B, Roose E. Aggregate stability as an indicator of soil susceptibility to runoff and erosion; validation at several levels. Catena. 2002;47:133–49.
Mathew RP, Feng Y, Githinji L, Ankumah R, Balkcom KS. Impact of no-tillage and conventional tillage systems on soil microbial communities. Appl Environ Soil Sci. 2012;2012:548620.
Carbonetto B, Rascovan N, Álvarez R, Mentaberry A, Vázquez MP. Structure, composition and metagenomic profile of soil microbiomes associated to agricultural land use and tillage systems in argentine pampas. PLoS One. 2014;9:e99949.
Miura T, Niswati A, Swibawa I, Haryani S, Gunito H, Arai M, Yamada K, Shimano S, Kaneko N, Fujie K. Shifts in the composition and potential functions of soil microbial communities responding to a no-tillage practice and bagasse mulching on a sugarcane plantation. Biol Fert Soils. 2016;52:307–22.
Navarro-Noya YE, Gómez-Acata S, Montoya-Ciriaco N, Rojas-Valdez A, Suárez-Arriaga MC, Valenzuela-Encinas C, Jiménez-Bueno N, Verhulst N, Govaerts B, Dendooven L. Relative impacts of tillage, residue management and crop-rotation on soil bacterial communities in a semi-arid agroecosystem. Soil Biol Biochem. 2013;65:86–95.
Souza RC, Cantão ME, Vasconcelos ATR, Nogueira MA, Hungria M. Soil metagenomics reveals differences under conventional and no-tillage with crop rotation or succession. Appl Soil Ecol. 2013;72:49–61.
Souza RC, Hungria M, Cantão ME, Vasconcelos ATR, Nogueira MA, Vicente VA. Metagenomic analysis reveals microbial functional redundancies and specificities in a soil under different tillage and crop-management regimes. Appl Soil Ecol. 2015;86:106–12.
Kandeler E, Tscherko D, Spiegel H. Long-term monitoring of microbial biomass, N mineralisation and enzyme activities of a Chernozem under different tillage management. Biol Fert Soils. 1999;28:343–51.
Staley T. Soil microbial biomass alterations during the maize silage growing season relative to tillage method. Soil Sci Soc of Am J. 1999;63:1845–7.
Balota EL, Colozzi-Filho A, Andrade DS, Dick RP. Microbial biomass in soils under different tillage and crop rotation systems. Biol Fert Soils. 2003;38:15–20.
Bronick CJ, Lal R. Soil structure and management: a review. Geoderma. 2005;124:3–22.
Kuntz M, Berner A, Gattinger A, Scholberg J, Mäder P, Pfiffner L. Influence of reduced tillage on earthworm and microbial communities under organic arable farming. Pedobiologia. 2013;56:251–60.
Pereira SB, Mota R, Vieira CP, Vieira J, Tamagnini P. Phylum-wide analysis of genes/proteins related to the last steps of assembly and export of extracellular polymeric substances (EPS) in cyanobacteria. Sci Rep-UK. 2015;5:14835.
Wooley JC, Godzik A, Friedberg I. A primer on metagenomics. PLoS Comput Biol. 2010;6:1–13.
De Vries M, Schöler A, Ertl J, Xu Z, Schloter M. Metagenomic analyses reveal no differences in genes involved in cellulose degradation under different tillage treatments. FEMS Microbiol Ecol. 2015;91:fiv069.
Putker F, Bos MP, Tommassen J. Transport of lipopolysaccharide to the gram-negative bacterial cell surface. FEMS Microbiol Rev. 2015;39:985–1002.
Ruiz N, Gronenberg LS, Kahne D, Silhavy TJ. Identification of two inner-membrane proteins required for the transport of lipopolysaccharide to the outer membrane of Escherichia coli. P Natl Acad Sci USA. 2008;105:5537–42.
Benedet M, Falchi FA, Puccio S, Di Benedetto C, Peano C, Polissi A, Dehò G. The lack of the essential LptC protein in the trans-envelope lipopolysaccharide transport machine is circumvented by suppressor mutations in LptF, an inner membrane component of the Escherichia coli transporter. PLoS One. 2016;11:e0161354.
Antunes LCS, Poppleton D, Klingl A, Criscuolo A, Dupuy B, Brochier-Armanet C, Beloin C, Gribaldo S. Phylogenomic analysis supports the ancestral presence of LPS-outer membranes in the Firmicutes. Elife. 2016;5:e14589.
Daims H. The family Nitrospiraceae. In: Rosenberg E, editor. The prokaryotes. Berlin, Heidelberg: Springer; 2014. p. 733–49.
Narita S. ABC transporters involved in the biogenesis of the outer membrane in gram-negative bacteria. Biosci Biotechnol Biochem. 2011;75:1044–54.
Skorupska A, Janczarek M, Marczak M, Mazur A, Król J. Rhizobial exopolysaccharides: genetic control and symbiotic functions. Microb Cell Factories. 2006;5:7.
Hay ID, Wang Y, Moradali MF, Rehman ZU, Rehm BHA. Genetics and regulation of bacterial alginate production. Environ Microbiol. 2014;16:2997–3011.
Preston GM. Plant perceptions of plant growth-promoting Pseudomonas. Philos T Roy Soc A. 2004;359:907–18.
Kwon K-J, Park K-J, Kim J-D, Kong J-Y, Kong I-S. Isolation of two different polysaccharides from halophilic Zoogloea sp. Biotechnol Lett. 1994;16:783–8.
Allison SD, Martiny JBH. Resistance, resilience, and redundancy in microbial communities. P Natl Acad Sci USA. 2008;105:11512–9.
Erridge C, Bennett-Guerrero E, Poxton IR. Structure and function of lipopolysaccharides. Microbes Infect. 2002;4:837–51.
Sutherland IW. Microbial polysaccharides from gram-negative bacteria. Int Dairy J. 2001;11:663–74.
Grafe M, Goers M, Sv T, Baum C, Zimmer D, Leinweber P, Vestergaard G, Kublik S, Schloter M, Schulz S. Bacterial potentials for uptake, solubilization and mineralization of extracellular phosphorus in agricultural soils are highly stable under different fertilization regimes. Envir Microbiol Rep. 2018;10:320–7.
Redmile-Gordon M, Brookes P, Evershed R, Goulding K, Hirsch P. Measuring the soil-microbial interface: extraction of extracellular polymeric substances (EPS) from soil biofilms. Soil Biol Biochem. 2014;72:163–71.
Cheng-Fang L, Dan-Na Z, Zhi-Kui K, Zhi-Sheng Z, Jin-Ping W, Ming-Li C, Cou-Gui C. Effects of tillage and nitrogen fertilizers on CH4 and CO2 emissions and soil organic carbon in paddy fields of Central China. PLoS One. 2012;7:e34642.
Jabro J, Stevens W, Iversen W, Evans R. Tillage depth effects on soil physical properties, sugarbeet yield, and sugarbeet quality. Commun Soil Sci Plan. 2010;41:908–16.
Angers DA, Bolinder MA, Carter MR, Gregorich EG, Drury CF, Liang BC, Voroney RP, Simard RR, Donald RG, Beyaert RP. Impact of tillage practices on organic carbon and nitrogen storage in cool, humid soils of eastern Canada. Soil Till Res. 1997;41:191–201.
Uksa M, Schloter M, Endesfelder D, Kublik S, Engel M, Kautz T, Köpke U, Fischer D. Prokaryotes in subsoil—evidence for a strong spatial separation of different phyla by analysing co-occurrence networks. Front Microbiol. 2015;6:1269.
Fierer N, Schimel JP, Holden PA. Variations in microbial community composition through two soil depth profiles. Soil Biol Biochem. 2003;35:167–76.
Griffiths RI, Whiteley AS, O'donnell AG, Bailey MJ. Influence of depth and sampling time on bacterial community structure in an upland grassland soil. FEMS Microbiol Ecol. 2003;43:35–43.
Hui N, Jumpponen A, Francini G, Kotze DJ, Liu X, Romantschuk M, Strömmer R, Setälä H. Soil microbial communities are shaped by vegetation type and park age in cities under cold climate. Environ Microbiol. 2017;19:1281–95.
Yamada T, Sekiguchi Y, Hanada S, Imachi H, Ohashi A, Harada H, Kamagata Y. Anaerolinea thermolimosa sp. nov., Levilinea saccharolytica gen. Nov., sp. nov. and Leptolinea tardivitalis gen. Nov., sp. nov., novel filamentous anaerobes, and description of the new classes Anaerolineae classis nov. and Caldilineae classis nov. in the bacterial phylum Chloroflexi. Int J Syst Evol Micr. 2006;56:1331–40.
Exley RM, Shaw J, Mowe E, Sun Y-h, West NP, Williamson M, Botto M, Smith H, Tang CM. Available carbon source influences the resistance of Neisseria meningitidis against complement. J Exp Med. 2005;201:1637–45.
McDonald IJ, Adams GA. Influence of cultural conditions on the lipopolysaccharide composition of Neisseria sicca. Microbiology+. 1971;65:201–7.
Galand PE, Lucas S, Fagervold SK, Peru E, Pruski AM, Vétion G, Dupuy C, Guizien K. Disturbance increases microbial community diversity and production in marine sediments. Front Microbiol. 2016;7:1950.
Huston M, Lawton JH. Biological diversity. The coexistence of species on changing landscapes. Nature. 1995;373:32.
Rashit E, Bazin M. Environmental fluctuations, productivity, and species diversity: an experimental study. Microb Ecol. 1987;14:101–12.
We thank Susanne Kublik and Anne Schöler for their help in performing the sequencing run. In addition, we would like to thank Lisa Guan for English proofreading.
The authors gratefully acknowledge the funding provided by the German Federal Office for Agriculture and Food (BLE) and the financial support for the Frick trial provided by the Swiss Federal Office for Agriculture (FOAG), the Software AG-Stiftung, the Stiftung zur Pflege von Mensch, Mitwelt und Erde and the Edith Maryon Stiftung. Moreover, this study was associated to the project Fertility Building Management Measures in Organic Cropping Systems (FertilCrop), which received funding from the CORE Organic Plus Funding Bodies, being partners of the FP7 ERA-Net project CORE Organic Plus.
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The raw sequencing data used in this study is available at the sequencing read archive (SRA) under the accession number PRJNA387672.
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Agricultural practices applied in the experimental field in Frick prior to sampling. (DOC 28 kb)
KO numbers related to EPS or LPS production found in the online Kyoto Encyclopedia of Genes and Genomes (KEGG) Orthology database (October 2016). (DOC 26 kb)
Details of the sequencing run. Shown are the numbers of obtained reads, total length of the reads and average read length per sample before and after quality filtering. “C” and “R” at the beginning of sample names stand for either “conventional tillage” or “reduced tillage”, respectively. The following “A”, “B” and “C” stand for the sampling depth (A – 0-10 cm, B – 10-20 cm and C – 20-50 cm). (DOC 43 kb)
NMDS ordination plots depicting taxonomic profiles of bacteria at the family level in conventional and reduced tillage-treated soils sampled at three different depths. Ellipses drawn around triplicates represent a 95% confidence level. Shown is A) overall community, and B) affiliation of genes related to EPS and LPS synthesis. Each point in the plot represents a different sample (n = 18), and the location of the points is based on Bray-Curtis distances. Taxonomic assignment was performed against the National Center for Biotechnology Information Non-Redundant (NCBI-NR) protein sequences database. Functional genes were assigned using hidden Markov models (HMMs) obtained from the TIGRFAMs and Pfam databases, and then sequences derived from the Kyoto Encyclopedia of Genes and Genomes (KEGG) Orthology database. (PDF 152 kb)
Bacterial families whose relative abundances and potential to produce EPS or LPS were significantly affected depth or interaction of tillage and depth. Significant differences between the treatments were determined by a multilevel model (n = 3, p < 0.05). (DOC 30 kb)
Comparison of the 35 most abundant bacterial families according to taxonomic annotations based on the NCBI-NR and SILVA databases. (PDF 248 kb)
Rarefaction curves of metagenomic datasets derived from conventional and reduced tillage-treated soils sampled at three different depths. Depicted is the number of assigned genes involved in EPS and LPS production as a function of sequencing depth. The genes were assigned using hidden Markov models (HMMs) obtained from the TIGRFAMs and Pfam databases, and then sequences derived from the Kyoto Encyclopedia of Genes and Genomes (KEGG) Orthology database. “C” and “R” at the beginning of sample names stand for either “conventional tillage” or “reduced tillage”, respectively. The following “A”, “B” and “C” stand for the sampling depth (A – 0-10 cm, B – 10-20 cm and C – 20-50 cm). (JPEG 1320 kb)
Boxplot depicting Shannon-Weiner index values which describe the diversity of bacterial families harboring genes wza, lptF and lptG at three depths. Significant influence of depth, but not tillage, was detected when applying a multilevel model analysis (n = 3). Therefore, tillage treatments were pooled for this plot. The influence of depth is symbolized with “*”. Significance levels are represented by the amount of symbols: 1 – p < 0.05, 2 – p < 0.01, 3 – p < 0.001. (PDF 117 kb)
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Cania, B., Vestergaard, G., Krauss, M. et al. A long-term field experiment demonstrates the influence of tillage on the bacterial potential to produce soil structure-stabilizing agents such as exopolysaccharides and lipopolysaccharides. Environmental Microbiome 14, 1 (2019). https://doi.org/10.1186/s40793-019-0341-7
- Soil aggregates
- Soil microbiome