Fungal diversity in canopy soil of silver beech, Nothofagus menziesii (Nothofagaceae)

Adventitious roots in canopy soils associated with silver beech (Nothofagus menziesii Hook.f. (Nothofagaceae)) form ectomycorrhizal associations. We investigated the extent to which canopy ectomycorrhizal communities contribute to overall diversity of ectomycorrhizal fungi associated with silver beech. Hyphal ingrowth bags were buried for 12 months in canopy and terrestrial soils of five trees at one site. We used amplicon sequencing of the nuclear ribosomal internal transcribed spacer 2 region (ITS2) to assess diversity of both ectomycorrhizal and non-ectomycorrhizal OTUs in hyphal ingrowth bags. There was a significant difference in ectomycorrhizal fungal community diversity between the terrestrial and canopy hyphal ingrowth bag communities. Ectomycorrhizal community composition of the terrestrial and canopy environments was also significantly different. Some ectomycorrhizal taxa were significantly differentially represented in either the terrestrial or canopy environment. The hyphal ingrowth bags also accumulated non-ectomycorrhizal species. The non-ectomycorrhizal fungi also had significantly different diversity and community composition between the canopy and terrestrial environments. Like the ectomycorrhizal community, some non-ectomycorrhizal taxa were significantly differentially represented in either the terrestrial or canopy environment. The canopy soil microhabitat provides a novel environment for growth of ectomycorrhizal adventitious roots and enables the spatial partitioning of ectomycorrhizal and non-ectomycorrhizal fungal diversity in the forest.


Introduction
Aerial soils that accumulate on branches of old-growth trees support a wide variety of life [1]. Canopy soils support epiphytes [2,3], epiphyte mycorrhizas [4,5], other soil microorganisms [6] and soil fauna [7]. Adventitious roots from the host may grow into canopy soil and, depending on the host species and other factors, these roots can be either arbuscular mycorrhizal [8], ectomycorrhizal [9,10] or non-mycorrhizal [11]. Thus, canopy soils host rich, diverse and variable fungal communities. These complex soil communities parallel their terrestrial counterparts, but the spatial separation of canopy soils from the ground and the invariably higher organic matter content of canopy soils [10,12]  The physical separation of the canopy soil from the terrestrial soil means that access to the canopy environment might be limited by dispersibility of propagules that originate from the terrestrial environment. For example, fungi that have wind-dispersed spores might have easier access to canopy soil than fungi that disperse by vegetative mycelial growth. Similarly, fungi that are dispersed by animals (e.g., grazing birds [22,23], bats, lizards or insects [22] hypothesised to disperse sequestrate fungi in New Zealand) might have differing access to the canopy soil, depending on whether the dispersers themselves access the forest canopy. Thus, there are many reasons why the canopy fungal communities could differ in aspects of their diversity and composition between terrestrial and canopy communities. We test the hypotheses that (i) ectomycorrhizal composition will differ between terrestrial and canopy soils, (ii) that canopy soils host lower beta-diversity than terrestrial soils.

Materials and methods
The New Zealand Department of Conservation granted permission to carry out the field work undertaken in this study. The Ngāi Tahu Research Consultation Committee at the University of Otago was consulted during the planning of this research.

Field site description
The field site was a mixed southern beech-podocarp cool-temperate rainforest~2 km south of the junction of the Jackson and Arawhata Rivers, 33 km southwest of Haast, Southern Westcoast, New Zealand (latitude −44.055, longitude 168.709, Fig 1). The map reference for the site is BZ11 563130 (Map NZTopo50-BZ11 Mt Pollux 1:50,000). The mean air temperature at Haast (Haast Aws station, latitude −43.861, longitude 169.007) is 11.5˚C (mean 2000-2001, 2003-2005, 2007-2015), and the mean annual rainfall is 3125 mm (mean annual rainfall average from years 2000, 2002-2016, 2011-2012) (data from CliFlo: NIWA's National Climate Database on the Web, http://cliflo.niwa.co.nz/, retrieved 1 December 2017). The site is significant because it is within Te Wāhipounamu: South West New Zealand World Heritage Area, an area with a long history of ecological and conservation research [24]. Five trees were selected for burial of hyphal ingrowth bags (Fig 1). Trees were selected on the basis of rope accessibility and safety for climbing to access branches with large accumulations of canopy soil. The location and dimension of each of the five trees sampled are given in S1 Table. The trees had extensive development of canopy soil on the branches (Fig 2). Based on a growth rate of 2.2 mm per year [25] and a diameter at breast height of > 1 m (S1 Table), the age of the trees is estimated at > 450 years, and while it is difficult to estimate the age of the canopy communities, it is expected that the most well-developed canopy soils are at least several hundred years old.

Sample collection
Hyphal in-growth bags were constructed of 2 × 2 cm 50 μm nylon mesh containing 1.2 g of acid washed sand (Unilab, Australia). Five hyphal ingrowth bags were buried in terrestrial soil within the dripline of each of the five trees (S1 Table) and at least 1 m away from the base of the trunk. Each bag was buried � 2 m apart at a depth of 4-5 cm. Five canopy bags were buried 4-5 cm deep in canopy soil of each tree, with each bag buried on a different branch (height above ground of each hyphal ingrowth bag is given in S1 Table, and ranged from 1.9-17.3 m above the ground). A total of 50 hyphal in-growth bags were buried in the canopy and terrestrial soils around the five selected trees. After a 12-month period the hyphal ingrowth bags were retrieved and kept at 4˚C for no longer than 48 hours before freeze-drying. Adhering soil was removed from the outer surface of each hyphal ingrowth bag. The content of each bag was placed into individual mortars and frozen by covering with liquid nitrogen. The mortars were then wrapped with aluminium foil, placed into a vacuum chamber and freeze-dried for 14 h. Dried samples were placed in resealable bags containing silica gel and stored at −20˚C until DNA extraction.

DNA extraction and sequencing
Prior to DNA extraction, the freeze-dried sand samples were mixed using a sterile spatula. Environmental DNA in the hyphal in-growth bags was extracted from 0.25 g of the sand using the PowerSoil DNA Isolation Kit (MoBio, Bio-Strategy, Auckland, New Zealand) as per the manufacturer's instructions. Isolated DNA from the hyphal ingrowth bags were diluted tenfold before PCR.
Amplicons were generated in a two-step process for sequencing on the Illumina MiSeq platform. Amplification of the nuclear ribosomal DNA from the ITS2 region was performed using the fungal specific primer pair ITS3_KY02 [26] and ITS4 [27] with Illumina TruSeq adapter sequences (IDT, Singapore and Custom Science Ltd, New Zealand). Each 50 μL first-round PCR reaction contained 10 μL of 5 × KAPA HiFi HotStart buffer (KAPA Biosystems, USA), 10 nmol of dNTP mix, 17.5 pmol of ITS3_KYO2 and ITS4, 0.2 μL of 10% bovine serum albumin, 1 U KAPA HiFi HotStart DNA Polymerase, 2 μL of a 1:10 dilution of gDNA and sterile H 2 O q.s..
Following the initial denaturing step at 95˚C for five minutes, 30 cycles of 98˚C, 47˚C and 72˚C each for one minute, with a final extension step of 72˚C for five minutes were performed on a thermocycler (Biometra TGradient, Göettingen, Germany). PCR products were visualized on 1.5% agarose gels.
Amplicons were purified using the Agencourt AMPure XP PCR purification system (Beckman Coulter, USA). DNA concentration was determined using a fluorimeter (Qubit, Invitrogen, USA) and the Qubit dsDNA HS assay kit. Amplicons were diluted to 1 ng/μL. Purified first-round PCR products were used as a template for second-round PCR. Each 50 μL reaction contained: 10 μL of 5 × KAPA HiFi HotStart buffer, 10 nmol of dNTP mix, 10 pmol each of primers with dual-indexed (i5 and i7) Illumina Nextera adapters, 1 U KAPA HiFi HotStart DNA polymerase, 2 ng of PCR product and sterile H 2 O q.s. Amplicons were visualized, purified and quantified as described above. Amplicon libraries were sequenced on the Illumina MiSeq using v2 chemistry allowing 250 bp paired-end reads by Otago Genomics Facility.
Negative controls comprising water-only template PCRs and PCRs of the same acid-washed sand used in the hyphal ingrowth bags were also prepared and sequenced in the same manner.

Bioinformatics
Paired-end reads were merged using USEARCH v11.0.667 [28] allowing a minimum of 97% similarity across the overlap. The samples were filtered at maximum expected errors (maxee) > 1.0 and the ITS2 variable region was extracted using ITSx v1.0.11 [29]. The reads were clustered at 97% using UPARSE and singletons were discarded [30]. OTUs were assigned taxonomy against the utax reference database 2.2.2019 using SINTAX [31] with a sintax_cutoff of 0.8, implemented in USEARCH. OTUs with high read counts (> 10 reads) in the control sample were deleted. This affected only four OTUs that were predominantly represented in the control sample. The samples were rarefied to the lowest reads per sample, 9,500 reads, in Qiime v1.9.1 [32], and separated into trophic guilds using FUNGuild v1.0 [33]. Guilds were combined into two groups: (i) ectomycorrhizal (using a strict criterion of selecting only the group 'Ectomycorrhizal' with a confidence rating of 'Highly Probable' or 'Probable') and (ii) non-ectomycorrhizal (comprising all other groups, excluding those OTUs that could not be assigned to functional guild). Because of the strict criterion for inclusion in the ectomycorrhizal group, it was expected that the non-ectomycorrhizal group would contain putative ectomycorrhizal OTUs with low confidence ratings. OTUs with an abundance of greater than 1% in either of the soil types that could not be assigned to functional group because of poor taxonomic assignment were searched against sequences in GenBank using BLAST [34] and reassigned in the FunGuild table (S2 Data). Those OTUs not assignable to any functional guild were excluded from further analysis. Identity of the top 25 most abundant ectomycorrhizal and non-ectomycorrhizal OTUs from both the canopy and terrestrial samples was crosschecked by conducting a search on UNITE [35] using massBLASTer. The species hypothesis corresponding to the sequences most similar to each OTU was selected. In some cases, we conducted closer phylogenetic exanimations of OTU sequences to determine the most accurate name where this disagreed with the most closely matching species hypothesis. Where no closely matching sequences could be named to species, we selected the species hypothesis from a higher taxonomic rank. A 1.5% threshold was selected for the most closely matching species hypothesis, unless a hypothesis at a lower threshold indicated different and more accurate identification.
The statistical analyses were performed in Qiime v1.9.1 and in R v3.3.2 using the packages phyloseq version 1.19.1 [36] and vegan version 2.4-2 [37]. The alpha diversity metrics: observed species, Simpson's diversity and Shannon-Weiner diversity, were calculated and plotted in phyloseq. Evenness was calculated by dividing the Shannon diversity by the log n of observed species. Because sample numbers differed in the terrestrial and canopy environments, each community was subsampled 1000 times to a maximum of 11 (the number of canopy samples) using resampling with replacement, calculating the mean for each replicate. Results were summarized by determining the mean, SD, median and range for each metric. The Mann-Whitney rank sum test, in the base R package, was used to test for statistical difference between alpha metrics. Beta diversity was calculated using Bray-Curtis dissimilarity and the differences between communities were visualized by non-metric multidimensional scaling (nMDS) in phyloseq. Adonis in vegan was used to test for differences in community composition between soil types, and betadisper was used to test for differences in dispersion of communities in each soil type by a permutation test for homogeneity of multivariate dispersions, with 999 permutations. Differential representation in the abundances of OTUs were tested using the Kruskal-Wallis test in Qiime.
Heat maps were generated in R with guidance from http://www.molecularecologist.com/2013/ 08/making-heatmaps-with-r-for-microbiome-analysis/ (accessed 7 April 2017) and using the packages: gplots version 3.0.1 [38], Heatplus version 2.20.0 [39], vegan version 2.4-2 and RColor-Brewer version 1.1-2 [40]. The Bray-Curtis matrix was clustered using average linkage hierarchical clustering and only OTUs with a relative abundance of greater than 5% in at least one sample were displayed in the heat map. Clustering was performed on the OTUs and samples.

Hyphal ingrowth bag recovery
Thirteen of the original 25 hyphal ingrowth bags were recovered from the 5 tree canopies and 20 of 25 terrestrial samples were recovered after the 12-month incubation period. Those that were not recovered were either missing or were found unburied at the site. Two canopy samples were unsuccessfully amplified by PCR, with the remaining 31 samples successfully amplified and prepared for sequencing.
Whilst the ECM fungal reads comprised 57% of the total reads across all samples (Table 1), the terrestrial samples had a greater (p < 0.001) proportion of ECM fungal reads (66%) than the canopy ECM fungal reads (39%) ( Table 2). The non-ECM fungal reads were relatively less abundant (p < 0.001) in the terrestrial samples (14%) and more abundant (p < 0.001) in the canopy samples (34%) ( Table 2). Those fungal reads not assigned to a functional group comprised 20% of the terrestrial reads and 26% of the canopy reads (Table 2).

Community diversity
The terrestrial ECM fungal communities were richer (p < 0.001) but less even (p < 0.001) than the canopy ECM communities, and the terrestrial ECM fungal communities had slightly higher Simpson (p < 0.001) and lower Shannon (p < 0.001) diversities (Table 3). Non-ECM Fungal diversity in canopy soil fungal communities were richer (p < 0.001) and more even (p < 0,001) in the terrestrial environment, and the terrestrial non-ECM fungal communities had higher Simpson (p < 0.001) and Shannon (p < 0.001) diversities (Table 3).

Community composition
Terrestrial fungal communities were different in composition from canopy fungal communities in both ectomycorrhizal (Fig 3) and non-ectomycorrhizal (Fig 4) fungal groups. In both cases, the canopy samples were associated with one side of the ordination space and the terrestrial samples the other side. The centroids of terrestrial and canopy fungal communities were significantly different for both ectomycorrhizal (P = 0.001, S2 Table) and non-ectomycorrhizal (P = 0.001, S4 Table) groups by the PERMANOVA test. The dispersions of samples in each soil type were not significantly different (ectomycorrhizal: P = 0.062, S3 Table; non-ectomycorrhizal: P = 0.434, S5 Table), so the difference between canopy and terrestrial fungal communities is interpreted to be due to community composition.

Dominant ectomycorrhizal fungi in terrestrial and canopy communities
Analysis of the terrestrial and canopy samples revealed a diverse array of ectomycorrhizal fungi (

Dominant non-ectomycorrhizal fungi in terrestrial and canopy communities
Analysis of the terrestrial and canopy samples revealed a diverse array of non-ectomycorrhizal fungi ( Table 5). The most abundant non-ectomycorrhizal OTU in terrestrial samples Fungal diversity in canopy soil Table 4. Top 25 OTUs of ectomycorrhizal species in terrestrial and canopy samples, ranked by the total number of reads. The name, species hypothesis (SH) and reference sequence are given for the closest matching sequence on UNITE. MisM = number of nucleotide mismatches between the query (OTU) and reference sequences; Q start/Q end = 5 0 /3 0 base positions of the OTU sequences; R start/R end = 5 0 /3 0 base positions of the reference sequences.

Sample-to-sample diversity in hyphal ingrowth bags
Displaying the sample-sample diversity as heat maps of ectomycorrhizal ( Fig 5) and non-ectomycorrhizal (Fig 6) fungi illustrates the patchiness of distribution of abundant OTUs. When the ectomycorrhizal OTUs were clustered using Bray-Curtis dissimilarity (Fig 5), the samples do not cluster into canopy and terrestrial groups. OTU2 (Cortinarius thaumastus) was Fungal diversity in canopy soil the most abundant terrestrial ectomycorrhizal OTU, but it was only present at high relative abundance in 5 of the terrestrial samples (collected from around the base of three different trees, Fig 5). Likewise, the dominant ectomycorrhizal OTU in canopy samples (OTU1, Laccaria violaceonigra) was only present at high relative abundance in some canopy samples, in addition to some terrestrial samples. There was no obvious relationship between Bray-Curtis dissimilarity of ectomycorrhizal samples and the tree from which each sample was taken (Fig 5).
The most abundant non-ectomycorrhizal OTU (OTU11, Mortierella humilis) was present at high relative abundance in most of the terrestrial samples (Fig 6). Canopy samples were either dominated by OTU5, which has similarity to the family Ceratobasidiaceae or OTU15, identified as the cryptococcal yeast Naganishia albida.

Discussion
The hyphal ingrowth bags accumulated fungi during the 12-month incubation period, a large proportion of which were identified as ectomycorrhizal taxa. The previously reported occurrence of adventitious canopy roots of the host trees [10] and the occurrence of mostly nonectomycorrhizal ectomycorrhizal epiphytic plant species at the site [2] mean that the ectomycorrhizal fungi found in the canopy hyphal ingrowth bags are most likely predominantly associated with the host tree itself. However, we can't exclude the possibility that some ectomycorrhizal fungi are associated with ectomycorrhizal epiphytes in the genera Nothofagus, Leptospermum or Kunzea. The discovery here of Cortinarius rotundisporus (OTU126) in the canopy hyphal ingrowth bags lends support to the idea that there were in fact myrtaceous host trees Fungal diversity in canopy soil growing as epiphytes, given that this fungal species associates only with Leptospermum and Kunzea and not Nothofagus [44].
Both aerial and terrestrial soils associated with Nothofagus menziesii are host to diverse communities of fungi, although the canopy soil communities of ectomycorrhizal and nonectomycorrhizal fungi being less rich than the terrestrial communities. he composition of the ectomycorrhizal community was different in each environment, with many species differentially represented to some degree in canopy or terrestrial communities. The finding that several ectomycorrhizal OTUs were significantly more represented in the terrestrial soil, whereas (under the Bonferroni-corrected p-value) only one OTUs had significantly greater representation in the canopy, could be explained by the canopy being less accessible to some species, or by each habitat being more or less suitable for those species. When the Kruskal-Wallis test was relaxed to use the FDR-corrected p-values, many OTUs were found to be differentially represented in both habitats, evidence that overall, the canopy soil increases habitat diversity for ectomycorrhizal species. Thus, the canopy soil represents a unique and additional, albeit slightly less-rich habitat for ectomycorrhizal fungi in this old-growth forest. By starting with bags containing only acid-washed sand, the technique allows the sampling of accumulated fungi that actively grew into the bags over the period of incubation. While the community of Fungal diversity in canopy soil fungi in the hyphal ingrowth bags may be different to that detected by other methods (e.g. [18]), it serves a valuable comparative purpose.
It was expected to find non-ectomycorrhizal fungi in the hyphal ingrowth bags. Initially lacking carbon, the bags would have slowly accumulated carbon as fungi grew into the bags and subsequently died, providing a carbon source for later inhabitants of the bags. The hyphal ingrowth bags in the present study were incubated in situ for 12 months, so it is plausible that senescence of early colonising fungi would have occurred. Despite not being the target guilds of the study, it is notable that the non-ectomycorrhizal fungal communities also differed between canopy and terrestrial habitats, being less rich in the canopy than the terrestrial environment (the same pattern as the ectomycorrhizal fungal communities), and less even than the terrestrial communities (the opposite situation to the ectomycorrhizal fungal communities). Interestingly, while more ectomycorrhizal OTUs were significantly more represented in the terrestrial environment (55% of the differentially represented OTUs) than the canopy (45% of the OTUs), the non-ectomycorrhizal species showed the opposite pattern, with only 37% of the terrestrial OTUs significantly more represented in the terrestrial environment and 63% of the OTUs in the canopy environment. This difference between ectomycorrhizal and non-ectomycorrhizal patterns could be explained by the relative influence of the edaphic environment on ectomycorrhizal and non-ectomycorrhizal fungi. The supply of carbon to ectomycorrhizal fungi by the host roots means that those fungal species may have less reliance on the soil for this important element, whereas the non-ectomycorrhizal species (that span soil saprophytes, insect-associated fungi, parasites, and many other guilds) could be much more influenced by the soil environment, either directly because of carbon availability, or indirectly via the soil being host to other organisms. It is still possible that the ectomycorrhizal communities are too influenced by the soil organic matter. It is notable that the ectomycorrhizal communities in both canopy and terrestrial environments included many species of Cortinarius, with 15 out of the 25 most abundant OTUs in the canopy samples belonging to that genus, and the most abundant terrestrial OTU. Cortinarius may have a role in degradation of organic matter in soils due to the possession of class II peroxidases that degrade lignin [45]. The high organic matter content of the canopy soils may be driving ectomycorrhizal species assemblages in that environment by providing a substrate better exploited by fungi that can take advantage of it.
It is acknowledged that the non-mycorrhizal fungi in the hyphal ingrowth bags are a small and unusual subsample of the true diversity of non-ectomycorrhizal soil fungi, because we did not directly sample these fungi from the soil, but rather indirectly from the hyphal ingrowth bags. However, given that the hyphal ingrowth bags were uniform in the canopy and terrestrial sites, the patterns seen here for both ectomycorrhizal and non-ectomycorrhizal fungi do reflect the different source populations of fungi in either environment, and for that reason the patterns observed for both groups of fungi do have biological and meaningful relevance. Diversity of non-ectomycorrhizal fungi in Australian native mixed forest was compared with adjacent Araucaria plantation forest in Australia [46], measuring diversity using both total DNA extracted from soil and from hyphal ingrowth bags. The total soil fungal communities were found to be more dissimilar between treatments than the communities sampled from hyphal ingrowth bags, indicating that the hyphal ingrowth bags did accumulate particular groups of fungi. The fact we retrieved distinctly different non-ectomycorrhizal communities from hyphal ingrowth bags in the present study indicates that the source populations of fungi in the canopy and terrestrial environments are distinctly different. The large difference in organic matter between canopy and terrestrial environments, and the presence of canopy epiphytes, are likely factors affecting the different communities of fungi.
Twenty-two percent of the sequence reads recovered from the hyphal ingrowth bags (representing 71% of the OTUs) were not assigned to any functional group. Some of these reads were determined to be non-fungal or of very low identity to any sequence on GenBank, and thus were difficult to deal with in any systematic way. Further, it is possible that at least some of these are erroneous sequences generated by PCR and sequencing errors, and future work could involve the identification and exclusion of these [47]. In previous studies using cloning of DNA amplified from hyphal ingrowth bags, higher proportions of OTUs were found to belong to ectomycorrhizal fungi. For example, at least 88% of clones from hyphal ingrowth bags buried in soil in Australian Eucalyptus pilularis forest were from ectomycorrhizal families [17], whereas in the present study, only 9% of total OTUs and 57% of total reads could be assigned to ectomycorrhizal taxa. Potential explanations for the lower proportion of ectomycorrhizal reads in the present study are many and could be related to inherent differences in fungal communities associated with the different tree species at each site, or more likely differences in the sequencing methodologies used. The Illumina sequencing used in the present study detected 294,500 sequences, compared with 800 clones analysed in the Eucalyptus study, so this 370-fold increase in sequences has likely detected many more rare taxa, an acknowledged feature of next-generation sequencing studies [48]. Thus, sequencing errors and increased detection of rare and poorly known OTUs are likely contributors to the lower proportion of ectomycorrhizal fungi in hyphal ingrowth bags in the present study.
That canopy soils are rich in ectomycorrhizal fungi accords with our earlier root tip-survey in canopy soils at the same locality and with the same host tree species [10]. We did not quantify the proportion of ectomycorrhizal root tips or total mycelial biomass in the canopy versus terrestrial soils at this site, so it is not possible to address the absolute contribution of each habitat to the overall ectomycorrhizal community associated with these trees. In a Costa Rican tropical montane rainforest [49], living fine adventitious roots in the canopy of Quercus copeyensis trees comprised only < 0.04% of the biomass of living fine terrestrial roots, and were thus regarded as having a negligible contribution to the total fine root biomass of the stand of trees. Notably though, the Q. copeyensis canopy roots were not ectomycorrhizal, in contrast to the heavily colonized terrestrial roots, and thus the canopy roots may lack the support of ectomycorrhizal fungi to exploit the canopy soil habitat. The proportional biomass of canopy soils worldwide is thought to be relatively low [1], but a New Zealand study [2] close to the site of the present study found high biomass associated with another forest tree, D. dacrydioides, however this was not quantified for the Nothofagus trees in the present study. The canopy soil of N. menziesii does host a wide range of ectomycorrhizal species and should not be discounted in terms of its contribution to the richness of ectomycorrhizal fungi associated with these trees. In considering the ecosystem services the canopy habitat provides to the ectomycorrhizal fungal community, the canopy communities may act as a reservoir for ectomycorrhizal species, from which the terrestrial communities recruit as canopy individuals fruit or are dispersed vegetatively. Recruitment to the canopy from the terrestrial habitat is also possible, and the differential representation of many OTUs shown here indicates that (i) beta diversity is increased by the existence of the canopy community, and (ii) that there may be limitations to recruitment of some species from one habitat to the other. In the present study, it was difficult to control for stochastic processes with only five trees sampled, and a multi-site study to determine how generally applicable these phenomena are would be of value. The identification of ectomycorrhizal OTUs as largely indigenous (endemic or Australasian) was typical of the biogeography of the region [50], with strong affinities with NZ, and representatives from Australia, South America and some biological invaders from the Northern Hemisphere. Of potential biosecurity importance to New Zealand was the discovery of Hebeloma hiemale in the hyphal ingrowth bags. This species has been reported from New Zealand previously (including PDD88816, GenBank accession GQ86951 from Salix caprea L. [41] and OTA60226, GenBank accession JX178629 from under introduced Quercus sp. at Oakune, New Zealand, erroneously identified as H. sacchariolens in Teasdale et al. [51]). Hebeloma hiemale has a wide host range, including conifers and angiosperms [41]. The discovery here of H. hiemale in hyphal ingrowth bags from Nothofagus-associated soil indicates H. hiemale is a potential symbiont with this New Zealand native tree.
Ectomycorrhizal roots and fungi slow the soil carbon cycle, through competition with decomposers for nitrogen [52]. In an old-growth forest like that in the present study, where canopy soil accumulation is extensive, decreased decomposition in the canopy soil of trees where the adventitious canopy roots are ectomycorrhizal may contribute positively to the above-ground forest carbon budget, more so than the canopy soil of non-ectomycorrhizal host trees. How auto-and heterotrophic nitrogen-fixing bacteria contribute to canopy soil nitrogen, and how this relates to fungal diversity, organic matter accumulation and decomposition, may improve our understanding of carbon and nutrient dynamics in these forests.