The cyanobacterial role in the resistance of feather mosses to decomposition--toward a new hypothesis.

Cyanobacteria-plant symbioses play an important role in many ecosystems due to the fixation of atmospheric nitrogen (N) by the cyanobacterial symbiont. The ubiquitous feather moss Pleurozium schreberi (Brid.) Mitt. is colonized by cyanobacteria in boreal systems with low N deposition. Here, cyanobacteria fix substantial amounts of N₂ and represent a potential N source. The feather moss appears to be resistant to decomposition, which could be partly a result of toxins produced by cyanobacteria. To assess how cyanobacteria modulated the toxicity of moss, we measured inhibition of bacterial growth. Moss with varying numbers of cyanobacteria was added to soil bacteria to test the inhibition of their growth using the thymidine incorporation technique. Moss could universally inhibit bacterial growth, but moss toxicity did not increase with N₂ fixation rates (numbers of cyanobacteria). Instead, we see evidence for a negative relationship between moss toxicity to bacteria and N₂ fixation, which could be related to the ecological mechanisms that govern the cyanobacteria-moss relationship. We conclude that cyanobacteria associated with moss do not contribute to the resistance to decomposition of moss, and from our results emerges the question as to what type of relationship the moss and cyanobacteria share.

Introduction

Symbiotic relationships between plants and microbes have been proposed to be important drivers of evolution [1]. Cyanobacteria are widespread and well-known symbionts, colonizing bryophytes, lichens and higher plants [2], [3], [4]. Cyanobacteria are facultative autotrophs, generally fixing atmospheric carbon (C) and nitrogen (N), but are also known to use host-C through symbiotic relationships [4]. The general assumption is that cyanobacteria-plant associations are mutualistic symbioses: the plant host receives N in the form of ammonium (NH4 +) or amino acids and in return provides carbohydrates, shelter and protection [5], [6], suggesting ecological specialization where the cyanobacteria down-regulate their own photosynthesis [3], [7].

In the northern boreal forest, atmospheric N deposition is generally low (1–3 kg N ha−1 yr−1), however, mosses colonized by N2 fixing cyanobacteria may contribute a further 2 kg N ha−1 yr−1, thus representing a major N input pathway in this pristine environment [8], [9]. Due to the strong N limitation of these ecosystems [10], the moss-cyanobacteria association characterizes the productivity of the ecosystem as well as its biogeochemical budget. One example is the relationship between one of the dominant primary producers in mid- to late succession boreal forests [8], the feather moss Pleurozium schreberi (Brid.) Mitt., and associated cyanobacteria. Substantial amounts of atmospheric N2 are fixed by cyanobacteria colonizing P. schreberi [8]. However, this process is sensitive to N inputs: higher N input through deposition results in lower numbers of cyanobacteria in the feather mosses and, consequently, in lower N2 fixation rates [9], [11], [12].

In spite of their dominant presence as a ground cover in the boreal forest ([8], [12], feather mosses are consumed by very few herbivores [13]. Although other bryophytes have been found to be even more resistant to decomposition [14], [15], it has been noted that even the herbivores that graze mosses appear to specifically avoid the ubiquitous P. schreberi and Hylocomium splendens [16]. Additionally, moss litter is known to be highly resistant to microbial decomposition in high latitude ecosystems [17]. However, the low quality of moss as a substrate or food source [13], [17] appears to be an insufficient explanation for the lack of utilization of this ample potential resource. The cyanobacteria that associate with feather mosses are known to produce toxins [3], [18], [19], which thus could play an important role in the resistance of mosses to grazing and decomposition. This would be a hitherto unrecognized dimension of the relations between feather moss and their cyanobacterial colonizers.

In this experiment we assess the contribution by cyanobacteria to the resistance to decomposition characteristic for mosses. More precisely, we hypothesize that moss toxicity increases with higher levels of cyanobacterial colonization and activity (N2 fixation). To assess this hypothesis, we used a microbial bioassay to estimate the toxicity of P. schreberi by determining its propensity to inhibit soil bacterial growth [20], [21], [22] across a gradient of cyanobacterial colonization in similar mid-later succession boreal forests in northern Sweden.

Materials and Methods

Sampling

We used shoots of the feather moss P. schreberi from six independent sites (all>1 km apart) distributed in four different mid- to late succession forests (Dötternoive, Borup, 2 sites from Nyvall, 2 sites in Kuottavare, more than 200 m apart; permission to sample granted by Norrbotten County Administrative board, Sweden, to Prof. M.C. Nilsson, Swedish Agricultural University, Umeå, Sweden) in Northern Sweden that have been shown to encompass a wide range of different N2 fixation rates needed for our experiment [12]. The sites were chosen to be as similar as possible in other aspects, and include a tree community of similar age (150–300 years; see [8], [12], [23]), successional stage, and nutrient status. The sites were located between latitude 64–65°N and longitude 18–19°E and have been described previously [8], [12], [23] (see also Table 1). Mean annual temperature and precipitation were 1 °C and 570 mm, respectively. The vegetation consists of Pinus sylvestris; Picea abies; Vaccinium vitis-idaea; V. myrtillus; Empetrum hermaphroditum; H. splendens and P. schreberi. Soils at the sites are classified as Typic Haplocryods (FAO, Cambic Podzol). While we are not able to exclude the possibility that other factors in addition to cyanobacterial colonization and N2 fixation activity were different among the six studied sites, it is not evident that any such factors could also have directly affected the mosses propensity to inhibit bacterial growth.

Table 1

Mean values (N = 18)±SE of the main soil properties from the moss- sampling sites in Northern Sweden.

pH	TC	TN	C/N	DOC	DON	DIN
4.4±0.3	369±23	11±3.6	48±1	1.46±0.17	0.02±0.02	0.002±0.0002

Data for soil nutrients are given in mg g−1 soil dry weight.

TC = Total Carbon; TN = Total Nitrogen; DOC = Dissolved Organic Carbon; DON = Dissolved Organic Nitrogen; DIN = Dissolved Inorganic Nitrogen. C/N is the ratio between TC and TN.

N2 fixation

N2 fixation was measured using a 15N calibrated acetylene reduction assay [24] as previously described [23]. Briefly, 10 moss shoots(>800 leaves shoot−1) from each site were placed in a 20 ml tube, sealed and 10% of the headspace was replaced with acetylene. Moss samples were incubated for 24 h at room temperature. Ethylene generated in the headspace by the cyanobacterial nitrogenase enzyme was measured by gas chromatography equipped with a flame ionization detector (Varian, Santa Clara, USA). The fresh moss shoots were ground using a ball mill (2 min., 30 s−1) forming a moss slurry, which was subsequently used in the bacterial growth assay to determine toxicity (below). Until processing, samples were kept at 4°C.

Cyanobacterial counts

Five different fronds with 10 leaves each were counted per sample, and moss leaves were destructively harvested from the fronds through scraping to enable microscopy counting. Cyanobacteria cells were then counted using an ultraviolet-fluorescence micrograph (Zeiss Axiophot 2 fluorescence microscope with 20× magnification) with a green filter. Cyanobacteria possess auto-fluorescent phycobiliproteins to capture light; therefore no staining is needed to visualize them using a fluorescence microscope.

Soil bacterial growth and toxicity assay

Soil bacterial growth rates were estimated using the thymidine incorporation technique [25], [26]. The reason to use the thymidine incorporation technique as opposed to leucine incorporation technique was that the latter is susceptible to confounding isotope dilution effects in plant tissue samples, which the present assay would be sensitive to. I.e., non-radioactive leucine concentrations were likely to scale with the moss-addition, causing unwanted isotope dilution effects. The determination of moss toxicity was otherwise determined analogously to salt toxicity in [21]. Briefly, 2 g of wet weight (ww) of soil (a composite and homogenized sample of the soil from all sites) was mixed with 20 ml of distilled water. The soil suspensions were vortexed for 3 min and then centrifuged for 10 min at 1000 g to obtain a bacterial suspension in the supernatant. From the soil bacterial suspension, 1.35 ml was used for the thymidine incorporation measurements in 2 ml microcentrifuge tubes. Subsequently, 0.15 ml moss (see below) was added to the 1.35 ml of the bacterial suspension in the microcentrifuge tubes.

Eight different concentrations of moss was used for each sample to determine its toxicity to bacterial growth; 0, 0.14, 0.41, 1.2, 3.7, 11, 33, 100 mg moss ml−1 were used in the moss toxicity determination as final concentrations in the bacterial suspensions. Distilled water was added to the control and to dilute the moss in the dilution series. Thymidine (TdR; [Methyl-3H]thymidine, 25 Ci mmol−1, 1.0 mCi ml−1, Perkin Elmer) was added to a final concentration of 130 nM in the bacterial suspensions. The samples were then incubated at approximately 20 °C for 2 h. The incorporation of TdR was terminated by the addition of 75 µL of 100% trichloroacetic acid. Non-incorporated TdR was then removed as described in [26], and TdR incorporation was measured in a scintillation counter (Wallac EG&G, Milton Keynes, UK).

Chemical analyses

We also investigated the N concentration in moss tissue of samples collected along gradients of cyanobacterial N2 fixation in Pleurozium schreberi induced by road pollution in boreal forests (for N2 fixation data and additional details, see [12]). Moss samples were dried at 80 °C for 24 h and ground to a fine powder using a ball mill. Total N (TN) in moss samples were analysed by oxidative combustion using an elemental analyzer interfaced to a continuous flow isotope ratio mass spectrometer (IRMS) (Sercon Ltd., Cheshire, UK).

Total phenols were measured in moss tissue that was first ground by placing 1 g dry weight equivalent of fresh moss tissue in a ball mill and then suspended in 10 ml of distilled water. Samples were centrifuged at 4000 rpm and the supernatant analyzed for phenols by using the Folin and Ciocalteau's reagent [27] and absorbance measured at 725 nm using a microplate reader.

Statistical analyses and calculations

Toxicity values were expressed as the concentration resulting in 50% inhibition (EC50)) of the bacterial growth in the soil suspensions. This is a universally adopted concept to toxicology and central to all ecotoxicology (e.g. [20], [21], [22]). More toxic moss inhibited the bacterial growth at lower concentrations and, therefore, has a lower value of EC50 than a less toxic moss. The EC50-values of the bacterial communities were calculated using a logistic model, Y = c/[1+e (], where Y is the TdR incorporation rate, X is the logarithm of the moss concentration, a is the value of log(EC50), c is the TdR incorporation rate in the control, and b is a parameter (the slope) indicating the inhibition rate. Kaleidagraph 4.0 for Mac (Synergy software) was used to fit a logistic curve to the data using the equation. Relationships between variables of the different sites were investigated using regression analyses or using analysis of variance (ANOVA) with Tukey's HSD post hoc pair-wise comparisons using JMP 9.0 for Mac (SAS Institute, Cary, NC, USA).

Results

Toxicity

We were able to demonstrate clear dose-response relationships between bacterial growth and moss addition for the six sites studied here (Fig. 1), with lower bacterial growth following exposure to higher concentrations of moss. The relationship between bacterial growth and moss exposure could be modeled well using a logistic model (R = 0.99, 0.93, 0.96, 0.96, 0.95 and 0.84 for the six sites, ordered from low to high N2 fixation rates/cyanobacteria numbers). Higher concentrations of moss effectively inhibited bacterial growth as indicated by suppression of growth by 90% at the highest moss addition rate.

Figure 1

Inhibition of bacterial growth by differently concentrated Pleurozium schreberi solutions hosting different numbers of cyanobacteria and with that, different N2 fixation rates (A–F).

These dose-response relationships were used to establish indices for toxicity (EC50 values) that were used in subsequent analyses (Fig. 2). Data points are mean values±1 SE of two determinations, and the fitted logistic curves (see Material and Methods) are based on the eight moss-concentration levels (n = 8).

The EC50-values were used as indices for moss toxicity to bacterial growth. The EC50-values were positively related to the presence (cyanobacterial cell count, see below; P<0.05; R2 = 0.72) and activity (acetylene reduction, see below; P = 0.01; R2 = 0.81; Fig. 2) of cyanobacteria on the mosses. This means that moss-toxicity decreased with higher cyanobacterial numbers and N2 fixation activity.

Figure 2

Relation between EC50 values as an index for moss toxicity and N2 fixation rates in P. schreberi.

Lower EC50 values indicate higher toxicity, and vice versa. Shown are mean values ±SE derived from the inhibition curves (Fig. 1).

N2 fixation and cyanobacterial count

N2 fixation rates were found to scale linearly with the numbers of cyanobacteria in the mosses, ranging between 0 and 200 cells leaf−1 (P<0.0001; R2 = 0.94) (Fig. 3), where low counts corresponded to low rates, and vice versa, and where a N2 fixation rate of 0 µmol m−2 d−1 acetylene reduced corresponded to 0 cyanobacteria cells, and a N2 fixation rate of 91 µmol m−2 d−1 acetylene reduced corresponded to 200 cyanobacteria cells leaf−1 (16*104 cells shoot−1).

Figure 3

Numbers of cyanobacteria cells leaf in relation to acetylene reduction (µmol m d) in the feather moss P. schreberi.

Total phenols in moss tissue ranged between 5.4 and 9.0 mg phenol g−1 fresh weight (Table 2). No correlation was found between phenols and N2 fixation and cyanobacterial numbers or between phenols and EC50-values.

Table 2

Moss characteristics of Pleurozium schreberi-tissue collected in Northern Sweden.

	pH		C/N*		Phenols (mg g−1 fw)		Chlorophyll (SPAD units)*
Site	mean	se	mean	se	mean	se	mean	se
A	4.6	0.12	44	0.5	7	0.2	4.7	0.84
B	4.8	0.12	44	0.5	5.4	0.37	4.7	0.84
C	4.4	0.13	32	0.8	5.7	0.38	2.5	0.53
D	4.4	0.13	32	0.8	9	0.49	2.5	0.53
E	4.4	0.13	40	1	6.8	0.19	3.4	1.3
F	4.3	0.15	53	0.9	8.4	0.56	3.5	0.81

Values are means±1 SE of 3–6 determinations. * C/N and Chlorophyll concentrations were determined on the same samples for sites A and B, and C and D.

Across well-replicated (3 independent sites, 3 independent replicates in each) and steep N2 fixation gradients from 30±9 to 250±40 µmol acetylene reduced m−2 d−1 (reported in [12]) we saw no differences in moss N-tissue concentrations, which were 35±3.2 and 37±1.9 µg N g−1 moss across the same gradient. This showed that the moss-additions in our bacterial toxicity assay that differed in cyanobacterial colonization and N2-fixation rate were not confounded by variation in added N in our bacterial assay.

Discussion

The use of biomarkers has been an invaluable tool to directly assess the toxic effect of substances in the environment [28]. While the interpretation of toxicity assessments based on biomarkers must consider the particular sensitivity or tolerance of the organisms used, it is generally held that the small size of microorganisms (and high area per volume) make them particularly exposed to toxins and thus sensitive indicators of the substances' general toxicity [29]. Moreover, while single species tests can be strongly biased by the properties of the particular strains included and must be supplemented by a battery of tests of different organisms before their effects can be generalized, assessing whole bacterial communities (as in the present study) are more robust in principle: it takes advantage of the naturally highly diverse bacterial communities to provide a continuous toxicity response that is a powerful tool to accurately establish the general propensity of a substance to be toxic [30]. Indeed, previous comparative assessments have validated the use of bacterial growth to assess environmental toxicity (e.g. [31], [32], [33]).

Bacterial growth was universally inhibited by moss additions irrespective of cyanobacterial presence or activity, as shown by the clear dose-response relationship that could be established for all tested mosses. This validated that we could assess the toxicity of moss. We hypothesized that moss toxicity, as indicated by the propensity of mosses to inhibit bacterial growth, would increase with higher numbers of cyanobacteria present. What we found was that cyanobacteria did not contribute at all to the toxicity of moss to bacteria. We cannot rule out a higher susceptibility of the other major decomposer group, fungi, to the toxic potential of mosses. However, in a thorough assessment of the abundance of fungi (ergosterol concentration) in relation to a previously reported N2-fixation gradient across fire chronosequence in boreal forests in Northern Sweden (see [23]), we found no differences in fungal presence (J. Rousk & K. Rousk, unpublished). It might be reasonable to suppose that bacteria should be more susceptible than fungi to toxins based on their higher area per volume. However, the fungal role in the decomposition of mosses, and the fungal susceptibility to moss toxicity, still remains to be studied.

That moss can inhibit bacterial growth is not surprising, and probably is partly related to the inhibitory nature of constitutional plant compounds, such as phenols, which have a known inhibitory effect on microorganisms (e.g. [34]). Further, it is possible that phenol content could have been instrumental for much of the toxicity that moss exerted on bacteria in general, since moss from all six sites could effectively suppress bacterial growth at high concentrations (Fig. 1). However, moss phenol content could not be used to explain differences in the inhibition of bacterial growth with regard to presence of cyanobacteria, as phenol concentrations in moss samples did not correlate with cyanobacterial colonization or with moss toxicity (EC50 values). Moreover, toxins produced by cyanobacteria are not exclusively phenolic, rather the majority are alkaloids and cyclic peptides [18]. Addition of N can result in an inhibition of microbial activity [35], making the tissue concentration of N a putative confounding factor in our analysis. However, we find no differences in the N content of mosses with high compared to low N2 fixation rate, effectively falsifying this as an alternative explanation for the inhibition of bacterial growth.

The obtained results on the variation of moss toxicity are of a negative nature, lending no support to our hypothesis stating that cyanobacteria contribute to the toxicity of moss. However, rather than no relationship (i.e. no slope in Fig. 2), we have a suggestion for a higher toxic effect by mosses that was correlated with lower cyanobacteria numbers and activity. Could these results be used to guide our understanding of the hitherto elusive ecology of moss-cyanobacteria relations? A range of observations from previous experiments and field investigations could be combined with our here reported results to develop a way forward to address this.

P. schreberi collected in Wales (UK), exposed to relatively high rates of N deposition(>12 kg N ha−1 yr−1, [36]), are not colonized by cyanobacteria and with that, do not fix N2 (K. Rousk & T.H. DeLuca, unpublished). When stored in a laboratory this remained true, but when N starvation was experimentally induced (rinsing with de-ionized water) cyanobacterial colonization and N2 fixation both commenced. It has also been found that cutting off the rhizoids and dead moss associated with moss carpets (i.e. severing its N supply from the soil) and returning it to the forest floor leads to a significant increase in cyanobacterial colonizers and N2 fixation rates (T.H. DeLuca, unpublished results). Further, the cutting of moss carpets from N rich environments and subsequent transplantation to N poor environments results in colonization of moss leaves by cyanobacteria and increased N2 fixation [37]. Taken together, these and other observations suggest that a regulation of cyanobacterial colonization of moss is very sensitive to the environmental growth conditions of the moss.

A possible mechanism for the regulation of cyanobacterial colonization of moss is the production of toxic secondary metabolites [19], such as oxylipins, derived from fatty acids [38], [39]. It is possible that such compounds could be used to control the colonization by bacteria generally, including that of cyanobacteria. The underlying ecology and causality of such a regulation would be ambiguous, however. One possibility would be that moss actively down-regulates the production of toxins during times of N deficiency to enable colonization by cyanobacteria and with that, a cyanobacteria powered endogenous supply of the limiting resource. Another possibility would be that conditions of N deficiency compromised the moss' ability to defend against opportunistic microorganisms generally, and cyanobacteria with their independent N supply in particular. Both these scenarios would imply that we should expect an emerging pattern that should be validated with observation: Moss decomposition should be slower in environments with high ambient N input, where cyanobacterial colonization is lower. Unfortunately we are not aware of a comprehensive data-set where this prediction could be evaluated, emphasizing a knowledge gap that urgently needs to be filled. These forwarded hypotheses call into question the placement of the cyanobacterial-moss symbiosis on the mutualism – parasitism continuum, which presently is an active area of research [40], [41]. The substantial work on the mycorrhizal-plant symbiosis [42] could act as a lens through which to focus experimental work to resolve the ecological interactions between the associated moss and cyanobacteria.

To conclude, we find no support for any contribution by cyanobacteria to the ability of feather mosses to resist decomposition. Instead, our results suggest a negative relationship between moss toxicity and cyanobacterial colonization. Our findings generate novel questions regarding the type of relationship that characterizes the ecology of moss and cyanobacteria – mutualistic or parasitic symbiosis?