Soil microorganisms as bacteria and fungi provide important ecosystem services as primary decomposers of organic matter (Bardgett, 2005), and as symbionts assisting plants with nutrient uptake (Whitman et al., 1998; Smith and Read, 2008). Abundance as well as taxonomic and functional diversity of the microbial community is thus pivotal for the production, stability and resilience of any plant-soil system (van Der Heijden et al., 2008). In order to understand thoroughly the impact of environmental changes or management practices on microbial communities, we must understand the effect of specific measurable parametric changes that the microbial cells need to cope with.
Soil pH is consistently recorded as one of the most influential factors affecting microbial communities (Lauber et al., 2009; Rousk et al., 2009, 2010). Bacterial richness responds to soil pH in a bell-shaped fashion, where richness is highest in soils with near-neutral pH, and lowest in soils with pH higher than 8 or lower than 4.5 (Lauber et al., 2009). In addition, community composition is strongly determined by soil pH (Lauber et al., 2009; Rousk et al., 2010). The pH effects on bacteria have been reported in mesocosm laboratory studies (Bang-Andreasen et al., 2017; Cruz-Paredes et al., 2017b), field-scale studies (Rousk et al., 2010), and at continental- to global-scale studies (Fierer et al., 2009; Lauber et al., 2009; Delgado-Baquerizo et al., 2018). In contrast, pH effects on fungi are less pronounced, and the responses of fungal communities appear weaker than those of bacterial communities. However, the effect of pH on fungi is much less studied in comparison to effects on bacteria (Rousk et al., 2010; Leifheit et al., 2014; Tedersoo et al., 2014; Cruz-Paredes et al., 2017b). Still, pH appears to be a significant determinant for fungal communities, but typically not as the most important driver (Tedersoo et al., 2014; Bahram et al., 2018). In a global-scale study (Tedersoo et al., 2014), soil pH was one of the most important predictors of fungal richness. Specific fungal strains typically have a wider pH optimum, often covering a range of 5–9 pH units without significant inhibition of growth (Rousk et al., 2010; Bahram et al., 2018).
Application of wood ash on forest soil has been proposed to prevent acidification and nutrient depletion (Jacobson, 2003), improve plant production (Cruz-Paredes et al., 2017a; Johansen et al., 2021), and to recycle waste product (Huotari et al., 2015). Wood ash increases soil pH (Fritze et al., 2000; Perkiömäki and Fritze, 2002) and contains nutrients, e.g., phosphorus, calcium, potassium and magnesium, along with heavy metals, e.g., cadmium, zinc, and copper (Knapp and Insam, 2011). Wood ash additions are most relevant in conifer plantation systems on relatively poor soil, where applications will partly mitigate nutrient imbalances caused by repeated harvest and counteract the natural acidification happening in forest soils (Knapp and Insam, 2011). Wood ash induces changes in the microbial community structure (Perkiömäki and Fritze, 2002; Björk et al., 2010; Cruz-Paredes et al., 2017b) similar to those induced by increasing pH (Rousk et al., 2011). Increases in microbial activity may also occur after wood ash addition (Bååth et al., 1995; Perkiömäki and Fritze, 2002; Zimmermann and Frey, 2002; Mahmood et al., 2003; Insam et al., 2009). Even though wood ash does not contain N, the increased pH after application often leads to higher N availability because of increased mineralization of organically bound N (Vestergård et al., 2018; Mortensen et al., 2020; Johansen et al., 2021). Moreover, wood ash addition tends to shift microbial communities toward increased bacterial and reduced fungal dominance (Bååth et al., 1995; Perkiömäki and Fritze, 2002). Micro- and mesocosm experiments with increasing dosages of wood ash in forest soil showed that the soil bacterial community composition changed after wood ash application. Copiotrophic bacteria responded positively while oligotrophic and acidophilic bacteria declined (Bang-Andreasen et al., 2017).
Studies on the effects of wood ash on fungal communities are limited, most of them quantified changes in the concentration of PLFA 18:2ω6 (fungal marker), where minimal or no responses were recorded (Bååth et al., 1995; Perkiömäki and Fritze, 2002; Cruz-Paredes et al., 2017b). One microcosm experiment showed that fungi were less responsive than prokaryotic community to wood ash additions in forest and agricultural soil (Bang-Andreasen et al., 2020). For ectomycorrhizal fungal communities in particular, the addition of moderate levels of wood ash (3–7.5 t ha–1) only seem to result in minor changes in the community composition despite a significant pH increment (Kjøller et al., 2017; Cruz-Paredes et al., 2019). A single study by Klavina et al. (2015), however, documented a very significant community shift between wood-ash-treated and control plots, but based on a rather high dose (50 t ha–1).
Bacterial and fungal communities have rarely been co-analyzed from the same field samples across a steep pH gradient. Here, we therefore analyzed the community responses of bacteria and fungi in parallel over a local wood-ash-induced pH gradient ranging from 4 to 8. We applied strongly alkaline wood ash in dosages of 0, 3, 9, 15, 30, and 90 t ha–1 to replicated plots in a Picea abies plantation. We hypothesized that:
(1) Both bacterial and fungal richness and diversity will increase with wood ash application as pH approaches 7, but diversity may decrease at the most extreme dosages when pH approaches 8.
(2) Wood ash application gradually changes the community structure of both bacteria and fungi at higher pH values, but bacterial communities respond stronger and at lower dosages than fungal communities do.
(3) With wood-ash-introduced pH increase and addition of nutrients, copiotrophic bacteria will thrive in expense of oligotrophic, and acidophilic bacterial groups will decrease with pH increments.
(4) Likewise, with pH increment we expect changes in the fungal community away from known acidophilic groups toward taxa thriving at higher pH and higher soil fertility.
Materials and Methods
The study site was a Norway spruce [Picea abies (L.) Karst.] plantation located in central Jutland, Denmark (N 56°16.63, E 9°05.20), 51 m above sea level. The climate is temperate with a mean annual temperature of 8.4°C and a mean annual precipitation of 850 mm. The experimental site is a second-generation plantation established in 1957 on former heathland with a well-developed podzolization formed on a well-drained, sandy glacial till. Mosses dominated the forest floor; in particular Hypnum jutlandicum, Dicranum scoparium and Pleurozium schreberi (Ethelberg-Findsen et al., 2021). The few understory plants are mainly Deschampsia flexuosa and Vaccinium vitis-idaea. In a randomized split block design, we applied wood-ash in April 2014 to 2 m × 2 m plots at six different dosages: 0, 3, 9, 15, 30, 90 t ha–1 with five replicate blocks (n = 5) with a total of 30 samples. We distributed the ash evenly over the soil surface, as a single addition. The ash came from wood chip fuel mixed ash from a combustion plant in Brande, Denmark, the particle size was less than 1 mm, and the pH was 13. Details on the elemental composition can be found under MA-9c in Maresca et al. (2017).
One year after application, in April 2015, we took three samples randomly with a 5 cm auger to a depth of 5 cm within each 2 m × 2 m plot at least 30 cm from the edge. Samples spanned the organic horizon of the forest floor and included litter and moss when present. The samples were stored at 4°C and processed in the laboratory the day after collection. We pooled the three subsamples from each plot into one composite sample per plot, which we sieved (5 mm) and homogenized. Soil nutrients and pH of the homogenized composite samples were measured as in Vestergård et al. (2018). Soil for subsequent DNA extraction was frozen immediately after sieving and homogenizing.
DNA Extraction, Library Preparation and Sequencing
We extracted DNA from 3 g of frozen soil with the PowerMax Soil® kit (MoBIO, Carlsbad, United States). For amplifying the prokaryotic community, dual-labeled primers 515f and 806r (Caporaso et al., 2012) targeting the V4 region of the 16S rRNA gene were used. For amplifying the fungal communities, a fragment of rDNA (ITS2) was amplified using dual-labeled primers gITS7 and ITS4 (White et al., 1990; Ihrmark et al., 2012). The master mix for both bacterial and fungal amplification consisted of 0.3 μl of PCR BIO HIFI Polymerase (PCR Biosystems Ltd., London, United Kingdom), 6 μl of PCR BIO reaction buffer (PCR Biosystems Ltd., London, United Kingdom), 3 μl of BSA, 0.6 μl of dNTP (10 mM), 15.6 μl of dd H2O, 3 μl of the primer mix and 1.5 μl of DNA template. We made three independent PCR amplifications for each DNA sample. For bacteria, PCR conditions included 1 min denaturation at 95°C; 30 cycles of 15 s denaturation at 95°C, 20 s annealing at 50°C and 20 s elongation at 72°C; and a 5 min final elongation step. For fungi, PCR conditions were the same as for bacteria except that the annealing temperature was 56°C. For each sample, we combined PCR products from the three independent PCRs (using the same tag combinations, in total 60 different sequencing tags were used) and purified using Agencourt AMPure XP beads (Beckman Coulter, Indianapolis, United States) according to the manufacturer’s protocol. DNA concentrations were measured using Qubit (Thermo Fisher Scientific, Massachusetts, United States) and samples were mixed in equimolar concentrations to a total of 1,000 ng of DNA for one adapter ligation reaction. Ligation of adapters was done using TruSeq DNA PCR-free LT Sample Preparation Kit (Illumina, San Diego, CA, United States). Sequencing was performed on the MiSeq (Illumina) platform using 250 bp paired-end and spiked with 30% PhiX DNA, bacteria and fungi were analyzed in separate runs. All the sequences were deposited in the Electronic Research Data Archive (ERDA) at the University of Copenhagen (see section “Data Availability Statement”).
Molecular Characterization of the Bacterial and Fungal Communities
Demultiplexing of samples, including removal of primers, tags and adapter remnants, was carried out with a custom script based on cutadapt (Martin, 2011). OTU tables for both bacteria and fungi were constructed, using the general approach of Frøslev et al. (2017) by initial processing with DADA2 (Callahan et al., 2016) to identify exact amplicon sequence variants (ASV). For the fungi, this was then followed by ITS extraction with ITSx (Bengtsson-Palme et al., 2013) and subsequent clustering with VSEARCH (Rognes et al., 2016) at 98.5%—the consensus clustering level used to delimit species hypotheses (SHs) in the UNITE database (Kõljalg et al., 2005). Subsequently, a post-clustering curation using LULU was done (Frøslev et al., 2017). Taxonomic assignment of the fungal OTUs was done using the 2017 UNITE general FASTA release. We used 98, 90, 85, 80, 75, and 70% sequence identity for assigning OTUs to species, genus, family, order, or class and kingdom, respectively. Additionally, fungal guilds were determined using FUNGuild (Nguyen et al., 2016), and exploration types for ectomycorrhizal fungi based on the fungal traits database 1.2_ver_16Dec_2020 (Põlme et al., 2021). For the bacterial data, we used the unclustered ASVs from DADA2 as OTUs in following analyses, following taxonomic annotation using the RDP classifier against the Greengenes reference database v13.8. Singleton OTUs were removed.
Richness (number of observed OTUs) and diversity (Shannon diversity) were calculated based on a rarified number of sequences per sample (limit set from the sample with the lowest number of sequences 1,668 for bacteria and 3,002 for fungi), using the vegan package (Oksanen et al., 2015) in R (R Core Team, 2020). Regression analyses were conducted between wood ash addition and bacterial and fungal richness and diversity using the R function lm. Data that were non-normal (as per Shapiro–Wilk test), were log-transformed prior to statistical analyses. Data was also checked for homogeneity of variances (as per Bartlett’s test). Non-metric multidimensional scaling (NMDS) ordination analyses were performed with Bray-Curtis dissimilarity matrices originating from bacterial and fungal OTU tables with relative abundance data. The vectors of wood ash, pH, and inorganic N and P were fitted onto ordination space (Bray-Curtis NMDS) to detect possible associations between patterns of community structure and these variables using the envfit function from the vegan package (Oksanen et al., 2015). We used one-way ANOVA to test the effect of wood ash dosage on the Bray-Curtis dissimilarities between microbial communities in wood ash treated and control soil. Initially we tested for any block effects, but since there were none, these were omitted from the final models. In the case of significant differences, we tested pairwise differences with a Tukey’s HSD multiple comparison test. Moreover, significant differences between bacterial and fungal community composition were tested for the different wood ash dosages also using PERMANOVA on a Wisconsin standardized Bray-Curtis dissimilarity matrix with the R function adonis from the vegan package (Oksanen et al., 2015) and pairwise PERMANOVA was used to test pairwise differences using the function pairwise adonis (Martinez Arbizu, 2020). Furthermore, correlations of microbial richness, diversity, and wood ash treatments with pH and inorganic N and P were evaluated using Pearson’s correlations and p-values were the significance level of t-test. All statistical analyses were done in R version 4.0.3 (R Core Team, 2020).
Effects of Wood Ash Treatments on pH and Inorganic N and P
Wood ash addition to the forest soil increased soil pH significantly from 3.8 in control plots, to 7.7 in plots treated with 90 t ha–1 of wood ash (see Vestergård et al., 2018 for details). Besides soil pH, concentrations of NH4-N, NO3-N and PO4-P increased significantly with wood ash additions, from 1.46 to 18.97, from 0.14 to 5.95 and from 3.89 to 223.80 μg cm–3, respectively (Vestergård et al., 2018). Wood ash amendment and soil pH significantly correlated with the increasing concentrations of NH4, NO3, PO4 (data not shown). The strongest correlation was found between wood ash and pH (Pearson’s, r = 0.82, p < 0.001).
Richness and Diversity of Bacterial and Fungal Communities
We evaluated richness as observed number of OTUs, and diversity as the Shannon index. Bacterial richness (number of OTUs) varied between 153 and 228 (Table 1), but neither bacterial richness nor diversity differed significantly between treatments or correlated with any of the abiotic parameters above. Fungal richness increased from 106 at 0 to 158 at 90 t ha–1, however, differences were not significant. Fungal diversity correlated positively with both wood ash additions and pH, as well as ammonium, nitrate and phosphate concentrations (Pearson’s, r = 0.41, 0.43, 0.45, 0.38, 0.43, respectively, 0.01 < p < 0.05).
Table 1. Bacterial and fungal OTU richness and diversity (Shannon index) in the different wood ash additions.
Composition of Bacterial and Fungal Communities
As evident from the NMDS ordinations (Figure 1) there was a strong influence of soil pH (colors) on the composition of the bacterial and fungal communities across the gradient of increasing wood ash (shapes). pH aligned strongly with the first axis of the plot similarly to wood ash addition (Figures 1A,C). NDMS axis 1 correlated strongest with pH (Pearson’s, r = −0.9, p < 0.001) followed by wood ash, NH4, PO4, and NO3 (Pearson’s, r = −0.71, −0.71, −0.69, and −0.68, respectively, p < 0.001).
Figure 1. NMDS plot of Bray-Curtis dissimilarities between (A) bacterial communities (stress = 0.13) and (C) fungal communities (stress = 0.19) from samples from the different wood ash treatments (different shapes). Soil pH measured in the different samples is also indicated with a color scale. Average Bray-Curtis dissimilarities of (B) bacterial and (D) fungal communities of untreated plots (no wood ash addition) compared to plots treated with increasing wood ash additions. Different letters denote significant difference (p < 0.05) obtained from Tukey post hoc tests.
Likewise, the envfit analysis showed that pH correlated the best with the NMDS projections followed by the wood ash treatment and the nitrogen and phosphorus measurements (Table 2). The PERMANOVA test showed that wood ash dosage significantly affected both bacterial (pseudo-F5,24 = 2.1, R2 = 0.30, p = 0.001) and fungal (pseudo-F5,24 = 1.3, R2 = 0.22, p = 0.008) communities.
We plotted the average Bray-Curtis dissimilarities of the two microbial communities comparing control plots with plots treated with increasing amounts of wood ash (Figures 1B,D). For both communities, the average distance between the five replicated control plots was lower than 0.7. For bacterial communities, the rate of change was larger than for fungal communities and dissimilarity from control was significant from 9 t ha–1 (pH≈ 5) (Tukey test p < 0.001) (Figure 1B). Furthermore, another “breakpoint” occurred between 15 and 30 t ha–1 (pH between 5.9 and 6.8) and dissimilarity increased to over 0.9 for the 90 t ha–1 (pH≈ 7.7) compared with control (Tukey test p < 0.001). The fungal communities did not differ significantly from the control at dosages below 30 t ha–1 (Figure 1D) (Tukey test p < 0.001 for 30 and 90 t ha–1) and the overall difference never exceeded 0.8. Likewise, the pairwise PERMANOVA showed that bacterial communities from wood ash treated plots, differed significantly from the control plots at lower dosages than the fungal communities did (Table 3).
Table 3. Pairwise testing for significant difference in bacterial and fungal communities between increasing wood ash dosages.
Taxonomic Composition of Bacterial and Fungal Communities
We plotted the relative abundances of the ten most abundant bacterial phyla in the plots treated with increasing dosages of wood ash (Figure 2A). In control plots, Acidobacteria had the highest relative abundance (32%), however, with increasing dosages of wood ash, the relative abundance decreased significantly (one-way ANOVA, F5,24 = 12.8, p < 0.001). In contrast, the relative abundance of Bacteriodetes increased significantly (F5,24 = 12.7, p < 0.001) with increasing wood ash and reached a maximum (36%) at 30 t ha–1 (pH≈ 6.8). The relative abundance of Firmicutes also increased significantly (F5,24 = 6.0, p < 0.001) at the highest wood ash addition (pH≈ 7.7). Other phyla like Chloroflexi had significant (F5,24 = 3.3, p = 0.02) higher relative abundance at an intermediate addition (30 t ha–1, pH≈ 6.8).
Figure 2. Relative abundance of (A) most abundant bacterial phyla, (B) most abundant fungal genera, (C) different fungal guilds and (D) ECM exploration types across wood ash treatments.
Likewise, we compared the relative abundance of the most abundant fungal genera across the pH gradient (Figure 2B). As for bacteria, the results indicate three different responses to the increasing wood ash/pH increment. Tylospora and Piloderma are examples of genera decreasing in relative abundance from 23 and 8% in the control treatment to 6 and 0%, respectively, at the highest dosage (pH≈ 7.7) but differences were not significant. In contrast, genera as Hebeloma and Didymella were not detected in control plots but increased significantly at higher wood ash doses (F5,24 = 2.0, p = 0.04 and F5,24 = 3.0, p = 0.03, respectively). Finally, Amphinema and Russula were examples of bell-shaped responses where abundances peaked at intermediate wood ash additions but these were not significant.
Additionally, we partitioned the fungal community into trophic groups and functional guilds (Figure 2C). “Ectomycorrhizal” was the most abundant guild in all treatments, but the relative abundance of this guild decreased slightly with increasing wood ash additions. Other guilds, such as “Pathogen” and “Endophyte” increased significantly (F5,24 = 3.0, p = 0.003 and F5,24 = 3.0, p = 0.01, respectively) with wood ash additions. Note, however, that the increase in “Pathogen” mimics the increase of the single species Didymella aurea. Finally, we further partitioned “Ectomycorrhizal” into exploration types (Figure 2D); again, the most obvious changes, like the decrease of “medium-distance_fringe,” mimics the changes in Cortinarius across the treatments.
In this study, we applied increasing dosages of wood ash to an acid forest soil which resulted in a steep local pH gradient. This allowed us to map in parallel the dose-response functions of fungi and bacteria to pH. In line with previous studies, we found that while both bacterial and fungal communities responded significantly to pH, bacteria were both more sensitive and responded stronger to the pH increase than fungi (Rousk et al., 2010; Cruz-Paredes et al., 2017b; Bang-Andreasen et al., 2020).
Bacterial and Fungal Richness
We found no effects of wood ash or increasing pH on bacterial richness or diversity, while both fungal richness and diversity increased with higher wood ash dosages, and thus, increasing pH. Our hypothesis (1) that bacterial and fungal diversity would increase with increased pH was only partly supported. Furthermore, we did not see any negative effects on diversity at the highest pH levels, as we expected. In a global-scale study (Tedersoo et al., 2014), soil pH was one of the most important predictors of fungal OTU richness. This was similar to our study where fungal richness was positively correlated with soil pH. However, at the local scale, Rousk et al. (2010) found that in an arable soil both bacterial and fungal richness increased with pH (pH 4.0–8.3), but for fungi, this response was only marginal. In a microcosm study where wood ash was added in increasing dosages, an opposite trend was found, since bacterial richness and diversity decreased with increasing wood ash additions (Bang-Andreasen et al., 2017). However, it is important to mention that the doses applied were higher (up to 167 t ha–1) than in the present study, and that the response was evaluated almost immediately after the additions. In our study, there were no negative effects on either fungal or bacterial richness with application of wood ash, which once again demonstrate how resilient microbial populations are to perturbations (Bardgett and Caruso, 2020).
In accordance with our hypothesis (2), community composition of both bacteria and fungi changed with increasing amounts of wood ash. Dosages of 9 t ha–1 (pH≈ 5) of wood ash significantly changed bacterial communities, while significant fungal community changes were only observed at higher dosages (30 t ha–1) (pH≈ 6.8) in line with our expectations. Among the measured environmental parameters, pH was by far the major driver of the microbial communities, and we showed how the relative abundance of certain bacterial phyla and fungal genera changed with soil pH. Interestingly, we have previously shown that microbial biomass markers (ergosterol, fungal and bacterial PLFAs) did not change systematically with wood ash additions in samples from the same plots as used in this study (Cruz-Paredes et al., 2017b). The relative changes in abundances seen in this study therefore putatively indicate also changes in living biomass of those same groups.
Changes in community composition of bacteria and fungi due to wood ash, correlated with soil pH and concentrations of inorganic N. As mentioned above, bacterial taxa have much more narrow pH optima and a deviation of only 1.5 pH units can reduce the growth by 50% (Fernández-Calviño and Bååth, 2010). Hence, even relatively small pH changes can change competitive balances between bacterial populations and lead to rapid replacement of populations with different pH optima (Booth, 1985). In contrast, fungal taxa have wider pH optima with the growth of filamentous fungi being unaffected even when pH changes 5–9 units (Wheeler et al., 1991; Nevarez et al., 2009; Strickland and Rousk, 2010). Furthermore, as pH strongly influences proton-driving force across the cell membrane, this may also explain why bacteria in general respond stronger to pH changes than fungi. Soil bacteria are completely dependent on their local water-filled soil pore environment on μm scale (Bardgett, 2005) while fungi have the possibility to bridge through both water-filled and air-filled spaces in the soil, though nutrient uptake can only take place in the water film (Moore et al., 2011). In addition, fungi have the option to seek out many soil compartments in three dimensions, with their extension of mycelia. This may be particular relevant when a perturbation as application of wood ash is placed on top of the soil.
Bacterial Community Composition
The changes in the relative abundances of bacterial phyla with increasing wood ash are consistent with responses to pH increase (Lauber et al., 2009; Rousk et al., 2010). Similar to our results, Lauber et al. (2009) found that Acidobacteria had the highest relative abundance at lower pH. In addition, the relative abundance of Bacteriodetes increased with increasing pH. Besides increasing soil pH, wood ash adds nutrients to the soil. In line with our hypothesis (3), some of the bacterial taxa such as Bacteriodetes and Firmicutes, which increased in relative abundance with wood ash, comprises copiotrophic bacteria that could benefit from increasing nutrient availability (Fierer et al., 2007, 2012). On the contrary, oligotrophic groups such as Acidobacteria (Ho et al., 2017), decrease with wood ash additions, as shown in previous studies (Bang-Andreasen et al., 2017, 2020, 2021).
Fungal Community Composition
Previously, few studies have investigated how wood ash addition affect the total fungal community composition. Most previous studies have focused on ectomycorrhizal fungal communities (Taylor and Finlay, 2003; Klavina et al., 2015; Cruz-Paredes et al., 2019). Similar to our findings, a meta-analysis on the effects of liming and wood ash additions on ectomycorrhizal fungi showed that the relative abundance of Tylospora fibrillosa decreased in treated plots compared to control (Kjøller et al., 2017). The meta-analysis also showed that Piloderma croceum decreased in relative abundance in treated plots (Kjøller et al., 2017), while we found that this genus was completely absent at the highest additions. On the contrary, the genus Hebeloma was not present in control plots, but the relative abundance increased with wood ash addition. This is in line with previous observations in peat soils amended with wood ash (Klavina et al., 2015; Kļaviņa et al., 2016). Similarly, the genus Didymella was absent in control plots and increased in relative abundance with increasing wood ash levels. Tylospora, Piloderma and Cortinarius are known acidophilic fungi while at least some Heboloma are nitrophilic (Kjøller et al., 2017; Lilleskov et al., 2019) therefore decreases of acidophilic and increases of nitrophilic groups are in line with our last hypothesis (4).
Finally, we also looked at how wood ash additions affected the relative abundance of the different fungal guilds. In control plots, the most abundant guild was the “Ectomycorrhizal” (45%) but with increasing wood ash additions, the relative abundance of this guild was reduced to 34% in 90 t ha–1 (pH≈ 7.7). Still “Ectomycorrhizal” was the most abundant guild in all treatments (not taking the non-assigned into account). We also found that the relative abundance of the “Saprotroph,” “Pathogen,” and “Endophyte” guilds tended to increase with wood ash additions. The tendency of the relative abundance of saprotrophic fungi to increase on the expense of ectomycorrhizal fungi fits well with the increasing amounts of NH4 and NO3 with higher wood ash dosages observed (Vestergård et al., 2018). With improved availability of nutrients such as ammonia, nitrate and phosphorus the need for the plant to invest in their mycorrhizal partner likely decreases (Kiers et al., 2011).
We applied increasing amounts of wood ash to an acidic forest floor and thereby successfully manipulated the soil pH from the ambient ≈4 to ≈8. This allowed us to model the responses of both fungal and bacterial richness as well as the communities and specific taxa within these groups. Community composition changed significantly for both microbial groups with pH. As expected, bacteria were more sensitive to pH changes, responding at lower dosages, and changing more from the start position than fungi. Despite the community changes, richness was either constant (bacteria) or increased with pH (fungi) which indicates that the microbial communities remained diverse also with relation to function (as shown for functional groups of fungi). pH was by far the best descriptor for the observed microbial community changes, better than the wood ash dosages or the PO4 added with the wood ash. Still, we did not measure all possible elements or water-soluble ions and acknowledge that other unmeasured elements applied with the wood ash may have contributed to the changes observed. Finally, the lack of effects at the low (realistic) to even medium high dosages after 1 year of wood ash applications, allows us to conclude that the use of wood ash as a liming and fertilization treatment in forestry does not pose harmful effects on the investigated variables.
Data Availability Statement
The datasets presented in this study can be found in online repositories. The names of the repository/repositories and accession number(s) can be found below: https://erda.ku.dk/archives/e990eedc9f4e7ad453010efc81b31f70/published-archive.html.
CC-P and TB-A did the laboratory work. TB-A and TF performed the bioinformatic analysis and wrote sections of the manuscript. CC-P performed the statistical analysis. CC-P and RK wrote the first draft of the manuscript. All authors contributed to the conception, design of the study, manuscript revision, established the field experiment, read, and approved the submitted version.
This work was supported by the “Center for Bioenergy Recycling – ASHBACK” project (www.ashback.dk), funded by the Danish Council for Strategic Research (Grant No. 0603-00587B).
Conflict of Interest
The authors declare that the research was conducted in the absence of any commercial or financial relationships that could be construed as a potential conflict of interest.
All claims expressed in this article are solely those of the authors and do not necessarily represent those of their affiliated organizations, or those of the publisher, the editors and the reviewers. Any product that may be evaluated in this article, or claim that may be made by its manufacturer, is not guaranteed or endorsed by the publisher.
The Supplementary Material for this article can be found online at: https://www.frontiersin.org/articles/10.3389/ffgc.2021.781844/full#supplementary-material
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