Spatial Community Structure of Mountain Pine Beetle Fungal Symbionts Across a Latitudinal Gradient

Abstract

Symbiont redundancy in obligate insect–fungal systems is thought to buffer the insect host against symbiont loss and to extend the environmental conditions under which the insect can persist. The mountain pine beetle is associated with at least three well-known and putatively obligate ophiostomatoid fungal symbionts that vary in their environmental tolerances. To better understand the spatial variation in beetle–fungal symbiotic associations, we examined the community composition of ophiostomatoid fungi associated with the mountain pine beetle as a function of latitude and elevation. The region investigated represents the leading edge of a recent outbreak of mountain pine beetle in western Canada. Using regression and principal components analysis, we identified significant spatial patterns in fungal species abundances that indicate symmetrical replacement between two of the three fungi along a latitudinal gradient and little variation in response to elevation. We also identified significant variation in the prevalence of pair-wise species combinations that occur within beetle galleries. Frequencies of pair-wise combinations were significantly different from what was expected given overall species abundances. These results suggest that complex processes of competitive exclusion and coexistence help determine fungal community composition and that the consequences of these processes vary spatially. The presence of three fungal symbionts in different proportions and combinations across a wide range of environmental conditions may help explain the success of mountain pine beetle attacks across a broad geographic range.

Electronic supplementary material

The online version of this article (doi:10.1007/s00248-011-9841-8) contains supplementary material, which is available to authorized users.

Introduction

The study of symbioses is fertile ground for the exploration of ecological and evolutionary relationships between intimately associated organisms [1, 2]. Bark beetles in the genus Dendroctonus and their mutualistic ectosymbionts are well-known models of symbioses [1, 3]. One member of this group, the mountain pine beetle (MPB; Curculionidae: Scolytinae: Dendroctonus ponderosae (Hopkins)), is of particular interest for its complex multipartite symbioses and capacity for large-scale population irruptions [4]. Recent outbreaks and population expansions of MPB have resulted in broad-scale and unexpected damage to forests in western North America [5, 6]. The unprecedented scale, extent, and intensity of this recent outbreak highlight the need to better understand the MPB system and the interactions between the MPB and its fungal symbionts.

MPBs are known for their close association with a number of symbiotic fungal species that often coexist in multipartite relationships [7]. Fungi in the family Ophiostomataceae are the most well known and play a number of beneficial roles for the beetle host by providing nutrition, protection against tree defenses, and modifying environmental conditions within the tree [8–11]. While MPBs are known to carry a diverse microsymbiont fauna, the main ophiostomatoid associates in western Canada are Grosmannia clavigera (Robinson-Jeffrey and Davidson) Zipfel, de Beer, and Wingfield; Leptographium longiclavatum Lee, Kim, and Breuil; and Ophiostoma montium (Rumbold) von Arx [12, 13].

Given the importance of fungi to MPB survival and reproduction [8, 11, 14–16], a number of studies have focused on teasing apart the interactions among fungal symbionts and the MPB host. Previous studies have demonstrated that the abundance and composition of fungal symbionts associated with MPB vary in both space and time [7, 17, 18]. Presence and relative abundance of different symbionts are affected by environmental conditions, in particular temperature [7, 17, 19]. Specifically, G. clavigera has a lower optimal growth temperature than O. montium, and consequently is more abundant in cooler conditions than the latter [7, 20]. L. longiclavatum similarly becomes more abundant in northern climates, such as northwestern Alberta, while it decreases in abundance in southern latitudes [18], despite having a growth optimum similar to G. clavigera [13, 19]. Studies have also demonstrated that two MPB fungal symbionts, G. clavigera and O. montium, can coexist despite apparent symbiont redundancy [7, 21].

Given that the relative abundance of fungal symbionts can change across a study region and that these shifts are likely to affect MPB fitness [16], we sought to examine patterns of spatial and temporal heterogeneity in MPB fungal symbiont community composition at the northeastern edge of the current outbreak. We examined coexistence and competition among fungal species at regional spatial scales and further explored how this variation translated into landscape-level variation in fungal assemblages [22]. Until now, the majority of research has focused on MPB populations in northwestern USA and southern British Columbia (BC). However, the population expansion associated with the current outbreak is occurring in northern British Columbia and Alberta (AB) where less is known about patterns of fungal symbiont association and community composition.

To better understand the nature of symbiotic beetle–fungus associations at the northern and eastern edges of the MPB outbreak, we sampled 50 sites distributed along a latitudinal gradient in eastern British Columbia and western Alberta over the course of two MPB flights. This latitudinal gradient is strongly associated with a gradient in elevation. Given the combined influence of elevation and latitude on environmental conditions [23], we also examined the role of elevation in determining community composition. Our objective was to describe the biogeographic patterns of fungal community composition in this region. We focused on three specific questions: (1) How does fungal abundance and species composition vary along this latitudinal gradient? (2) Under what conditions do all three species (G. clavigera, O. montium, and L. longiclavatum) coexist and under which conditions are some species excluded? and (3)What degree of temporal variation do we observe between years in fungal abundance and species composition? Our broad-scale approach seeks to identify landscape-level processes that affect MPB symbiont composition, and this study represents one of the first to examine these community patterns using large-scale surveys of natural MPB populations. From previous work on fungal temperature tolerances [7, 19], we expected that the abundance of G. clavigera and O. montium would decrease with increasing latitude, with an opposing trend observed in L. longiclavatum. Furthermore, we expected to see temporal variation between years, given the temperature sensitivity of fungal growth.

Methods

Data Collection

A nested sampling design with three levels was used to survey fungal composition in regions with large numbers of newly, successfully attacked pine trees. Trees were identified by provincial ground or aerial surveys in eastern BC and western AB, respectively (Fig. 1; Table 1; Electronic Supplementary Material 1), as previously described in Roe et al. [24, 25]. Sampling occurred during two time periods, February–May 2007 (period 1) and September 2007–April 2008 (period 2), which represent independent dispersal flights of MPB during the 2006 and 2007 seasons, respectively. The three levels to this sampling design were (1) landscape, (2) sites within landscapes, and (3), individual trees within sites (Fig. 1; Electronic Supplementary Material 1). Landscapes were selected to represent a range of ecoregions [26] throughout the leading edge of the MPB outbreak, with up to five sites sampled in each landscape at a minimum 5 km apart (Table 1). Within each site up to ten green attacked trees (minimum 50 m apart) were sampled. Green attacked trees are those that show recent evidence of MPB attack, contain developing brood, and whose needles have not yet turned red or gray. From each tree, eight phloem + xylem disks containing sections of MPB galleries were obtained using a 10-cm hole saw and chisel. Disks were sampled systematically, with four disks removed at 0.5–1.0 m and the remaining disks removed at 1.3–1.6 m in the orientation shown in Electronic Supplementary Material 1. Disks were transported on ice back to the laboratory for fungal culturing.

Figure 1.

Location of collection sites for MPB fungal symbionts and the relative abundance of each fungal species scored in the 12 landscapes. Inset shows overall relative abundance; Gc, G. clavigera; Om, O. montium; Ll, L. longiclavatum. Landscapes, with one to six sites, as follows: CA, Canmore; CH, Cypress Hills; CN, Crowsnest Pass; FC, Fox Creek; FV, Fairview; G, Golden; GP, Grande Prairie; KY, Kootenay–Yoho; SW, Sparwood; TR, Tumbler Ridge; V, Valemount; WK, Willmore-Kakwa

Table 1.

Localities surveyed for mountain pine beetle fungal symbionts

Landscape	Province	Site	Perioda	Latb	Longb	Elevation (m)	Eco.c	Eco. namec	No. of trees
Fairview	AB	FV.a	1	56.128	−118.548	635	138	Peace Lowland	10
		FV.b	1	56.314	−119.892	721	138	Peace Lowland	7
		FV.c	1	56.182	−118.633	642	138	Peace Lowland	6
		FV.aa	2	56.599	−119.384	949	137	Clear Hills Upland	10
		FV.bb	2	56.158	−118.643	639	138	Peace Lowland	10
		FV.cc	2	56.991	−119.738	792	137	Clear Hills Upland	10
		FV.dd	2	56.469	−119.932	748	137	Clear Hills Upland	10
Tumbler Ridge	BC	TR.aa	2	55.539	−121.985	842	200	Central Can Rocky Mts	8
		TR.bb	2	54.913	−121.230	902	200	Central Can Rocky Mts	10
		TR.cc	2	55.321	−121.441	942	200	Central Can Rocky Mts	10
		TR.dd	2	55.275	−121.191	1,012	200	Central Can Rocky Mts	7
Grande Prairie	AB	GP.a	1	55.088	−118.756	579	138	Peace Lowland	10
		GP.b	1	55.056	−118.510	632	138	Peace Lowland	10
		GP.c	1	54.995	−119.222	683	138	Peace Lowland	10
		GP.aa	2	54.992	−118.614	607	138	Peace Lowland	7
		GP.bb	2	54.899	−119.369	764	143	W Boreal	11
		GP.cc	2	54.803	−119.789	888	143	W Boreal	10
Fox Creek	AB	FC.a	1	54.703	−117.021	708	143	W Boreal	8
		FC.b	1	54.651	−116.301	987	145	W AB Upland	7
		FC.c	1	54.480	−116.635	862	143	W. Boreal	6
		FC.aa	2	54.481	−116.635	786	143	W. Boreal	10
Willmore-Kakwa	AB	WK.a	1	53.713	−119.743	1,664	207	E Continental Ranges	10
		WK.b	1	53.776	−119.761	1,866	207	E Continental Ranges	9
		WK.c	1	53.826	−119.657	1,439	207	E Continental Ranges	10
		WK.aa	2	53.996	−119.526	1,622	207	E Continental Ranges	10
		WK.bb	2	53.650	−119.509	1,377	207	E Continental Ranges	10
		WK.cc	2	53.854	−119.584	1,547	207	E Continental Ranges	10
Valemount	BC	V.aa	2	52.882	−119.301	847	213	S Rocky Mtn Trench	10
		V.bb	2	52.853	−119.382	1,164	213	S Rocky Mtn Trench	10
		V.cc	2	52.963	−119.380	898	206	W Continental Ranges	10
Golden	BC	G.aa	2	51.074	−116.382	1,330	206	W Continental Ranges	11
		G.bb	2	51.361	−116.937	1,679	206	W Continental Ranges	10
		G.cc	2	51.495	−117.003	1,494	206	W Continental Ranges	10
Kootenay/Yoho	BC	KY.aa	2	50.912	−116.037	1,234	206	W Continental Ranges	10
		KY.bb	2	51.334	−116.550	1,190	206	W Continental Ranges	10
Canmore	AB	CA.a	1	50.859	−115.349	1,906	207	E Continental Ranges	10
		CA.b	1	51.111	−115.352	1,691	214	N Continental Divide	10
		CA.aa	2	50.932	−115.336	2,054	207	E Continental Ranges	10
		CA.bb	2	50.940	−115.153	1,579	214	N Continental Divide	10
		CA.cc	2	51.030	−115.243	1,426	214	N Continental Divide	10
		CA.dd	2	50.877	−115.347	1,953	207	E Continental Ranges	10
		CA.ee	2	51.128	−115.380	1,382	214	N Continental Divide	14
Sparwood	BC	SW.aa	2	49.680	−114.911	1,321	214	N Continental Divide	9
		SW.bb	2	49.840	−114.801	1,610	214	N Continental Divide	10
		SW.cc	2	49.894	−114.895	1,312	214	N Continental Divide	9
Crowsnest Pass	AB	CN.a	1	49.629	−114.696	1,422	214	N Continental Divide	7
		CN.aa	2	49.657	−114.552	1,510	214	N Continental Divide	3
		CN.bb	2	49.986	−114.495	1,697	214	N Continental Divide	2
		CN.cc	2	49.629	−114.434	1,548	214	N Continental Divide	5
Cypress Hills	AB	CH.aa	2	49.593	−110.036	1,357	160	Cypress Upland	6

^aPeriod 1: samples extracted from trees and beetles February–May 2007; period 2: samples extracted from trees and beetles September 2007–April 2008

^bGPS coordinates based on site centroids

^cEcoregions defined by the Ecological Stratification Working Group [25]

Fungal Culturing

Fungi were cultured from larval and adult (parental) MPB as well as from wood samples taken adjacent to individual MPB within galleries following the protocol described in Roe et al. [25]. A single gallery was sampled per disk to ensure that independent galleries were sampled, resulting in two isolations per parental gallery (i.e., one from the insect and one from an adjacent wood sample). Isolations were stored at room temperature and ambient light, and colonies were subcultured as they appeared (2–5 days, subculturing occurred most often at day 3). Colonies of the three most common fungal associates tended to appear within 2–3 days at room temperature [19], and isolation of individual colonies after longer incubation periods became problematic due to overgrowth by faster-growing species, as well as contamination by mites, bacteria, and other fungi (e.g., yeasts). Sub-cultures were plated onto malt extract agar and then incubated for 2–4 weeks at similar conditions before being scored for the presence of fungal associates. Individual species were identified based on morphological and microscopic traits of known MPB fungal associates, which were derived from original species descriptions and authenticated strains, as described in Roe et al. [25]. A small number of strains were morphologically ambiguous and were termed “intermediate.” Detailed descriptions of cultural and microscopic morphological traits used for identification are provided (Electronic Supplementary Material 2).

Given the uniform temperature and incubation period used in this methodology, it is possible that slower-growing, rare, or cryptic species were missed in these mixed-species cultures, favoring the identification of faster-growing, dominant species. To assess the success rate of morphotyping, identifications based on multilocus sequence typing (MLST) genotype data (GenBank GU370130-GU370344, HQ413347-HQ413650) for a subset of strains (n = 493) were contrasted with their initial morphotyping diagnoses. The methodologies and resulting multilocus sequence typing data were originally published in Roe et al. [24, 25], but an abbreviated summary is provided here. Representative strains were deposited in the University of Alberta Microfungus Collection and Herbarium (UAMH 10965-10970, 11000-11007, 11013-11020, 11035-11084, 11105-11119, 11134-11149), as described in Roe et al. [24, 25].

Analyses

We calculated the relative abundance of each of the three fungal species and species composition within individual galleries. Relative abundance describes the proportion of individuals scored as a species relative to the total number of isolates screened. Species composition describes the combination of species that were simultaneously found within an individual gallery. In this system, there are eight species combinations possible: G. clavigera alone, O. montium alone, and L. longiclavatum alone; paired combinations G. clavigera–O. montium, G. clavigera–L. longiclavatum, and O. montium–L. longiclavatum; all three in combination, G. clavigera–O. montium–L. longiclavatum; and zero species. We used the proportions of each of three combinations to describe changes in the fungal community in space and time. Relative abundance and composition were summarized at the level of sites nested within landscapes for a total of 50 sample sites within 12 landscapes (Table 1, Fig. 1). Given the spatial extent of the study area, we did not examine tree level variation and instead focus on broad biogeographic patterns.

Relative Abundance

We used principal components analysis (PCA) to visualize variation among sites in fungal community composition and to identify which species drive differentiation among sites. Ordination using PCA reduces the dimensionality of multivariate data, exposes intrinsic gradients, and allows such data to be interpreted diagrammatically [27]. Prior to analysis, the community data (abundance data pooled by site) were converted to relative abundance of the three species at each site and standardized using the Hellinger transformation [28]. PCA was then performed on the total set of standardized data using the rda function of the vegan package in R [29]. Significant PCA axes were identified using the broken stick criterion [30]. Following PCA, we fit vectors of latitude and elevation onto the ordination space to identify which axes and which species were most strongly correlated with the different gradients. Post-hoc vector fitting was done using the envfit function in the vegan package in R.

Rate of Change

Three linear mixed-effects regression models were used to describe the relationship of each species’ relative abundance to changes in latitude and elevation. Latitude and elevation were used as fixed effects while sample landscape was used as a random effect to account for additional landscape specific variation. Fixed-effect predictor variables were standardized to zero mean and unit variance prior to analysis. Regression models for all three species were significantly improved by the inclusion of the landscape random effect (data not shown). Three hypotheses based on previous research [e.g.,7, 17, 18] were tested using these models: (1) G. clavigera will decrease in relative abundance with increases in latitude, (2) O. montium will also decrease in relative abundance with increases in latitude, and (3) L. longiclavatum will increase in relative abundance with increases in latitude. Specific hypotheses regarding elevation were not tested because of the high degree of correlation with latitude and the lack of a consistent influence of elevation on fungal abundances as identified using the regression models described above. Analysis of covariance (ANCOVA) was then used to compare the rates of change (i.e., slopes) among pairs of the three fungal species in response to latitude. In particular, we were interested in ascertaining whether the rate of change in the abundance of G. clavigera from north to south was significantly different from the rate of change of L. longiclavatum from south to north. Because the rate of change in G. clavigera is negative, while that of L. longiclavatum is positive, we used the absolute value of the slope of L. longiclavatum for comparison (i.e., converted values to have a negative slope). The pair-wise ANCOVA tests used latitude and fungal species as predictor variables, and tested for a significant interaction effect between them. As in the single-species models described above, sample landscape was used as a random effect. All mixed-effect models were carried out using the lme function in the nlme package in R [31, 32] and were summarized using marginal sums of squares.

Differences Between Years

Because fungi were sampled over two sampling periods, we also compared relative fungal abundance in period 1 and period 2 to identify potential temporal variation. Similar to comparisons among the different species and their response to latitude, we used ANCOVA to test whether sampling period affected relative species abundance.

Species Coexistence

We used multiple Chi-square tests to test patterns of fungal species coexistence using species composition within galleries as a measure of coexistence. Specifically, we assessed the significance of differences in the proportions of each of the three pair-wise species combinations (i.e., G. clavigera–O. montium, G. clavigera–L. longiclavatum, O. montium–L. longiclavatum). However, because species varied in relative abundances, the differences in the proportions of each combination could be simply due to the varying probability of species co-occurrence. We also used a series of Chi-square tests to assess whether the observed occurrence of each species combination was different than expected given individual species abundances. In these tests, the null hypothesis was that the frequency of each pair-wise combination was proportional to the product of their individual abundances. Tests were conducted for the entire study area as well as for the northern and southern groups of sites. All statistical analyses were conducted in R [33].

Results

Over the two sampling periods, 2,852 MPB galleries were surveyed in 50 sites from 12 landscapes (Fig. 1, Table 1). Landscapes spanned 7.5° of latitude, from 49.5° to 57.0° N. Based on MPB distribution patterns, these landscapes formed two natural groups that matched the MPB distribution in the region: a northern group (Fairview, Tumbler Ridge, Grande Prairie, Fox Creek, Wilmore-Kakwa, and Valemount) and a southern group (Golden, Kootenay–Yoho, Canmore, Sparwood, Crowsnest Pass, and Cypress Hills). During the sampling periods, no MPBs were detected in the intervening area between Valemount, BC and Golden, BC. These groups also correspond to broad-scale phylogeographic patterns previously detected in G. clavigera, O. montium, and L. longiclavatum [24]. The number of sites surveyed per landscape ranged from one to seven. The majority of sites were located in lodgepole pine stands (Pinus contorta Douglas var. latifolia Engelmann), with the exception of Fox Creek, which was in a putative P. contorta Douglas var. latifolia Engelmann × Pinus banksiana Lamb. hybrid zone. The extent of this zone of hybridization is not well defined [34, and the references therein]. Since hybrids were determined morphologically, it is conceivable that trees of undiagnosed hybrid status were also sampled. Sampling between the two time periods was disproportionate. In period 1, 599 galleries were surveyed at 15 sites in six landscapes, while in period 2, 2,253 galleries were surveyed at 26 sites in 12 landscapes. Each gallery produced two samples, one from the beetle and one from gallery wood tissue. Given the timing of sampling (winter and early spring), the majority of insect isolates were obtained from larval (n = 2,375), rather than adult MPB (n = 557). No global differences in fungal species abundance were detected between larval and adult derived fungal samples (data not shown), so larval and adult data were subsequently pooled.

Morphotyping × Molecular Genotyping Success Rate

We contrasted initial morphological diagnoses with multilocus sequence data (i.e., MLST) derived identifications for a subset of cultures (n = 493) as described in Roe et al. [24, 25]. We identified differences between the morphotyping and genotyping success rates among the three fungal symbionts examined (Electronic Supplementary Material 3). Three main results were obtained from these comparisons. First, the overall success rate of morphological diagnosis was 74.6% (morphological diagnosis equals MLST genotype), although this success was not evenly distributed between species. Second, two undiagnosed MPB fungal associates were identified through MLST genotyping (Genlisea aurea and Leptographium terebrantis), although together they represent a small proportion (~5%) of the subsampled strains. Third, the majority of strains identified as morphologically intermediate were genotyped as L. longiclavatum (90.0%).

From a morphotyping perspective, 27.3% of strains initially identified as G. clavigera were misdiagnosed (giving a 72.7% morphotyping success rate), while from a genotyping perspective, 14.2% of the genotyped G. clavigera strains were mismorphotyped (genotyping success rate of 85.8%). In contrast, L. longiclavatum morphotypes were rarely misidentified (98.0% morphotyping success rate) but had the lowest genotype success rate (58.0%) due primarily to the large number of intermediate strains. O. montium morphotypes were occasionally misidentified (85.1% morphotyping success rate) but had the highest genotyping success rate (95.8%).

Relative Abundance

The relative abundance of fungal species for each landscape and sampling period are summarized in Table 2. In total, 5,717 isolates were identified. Of these isolates, 2,270 (39.7%) were G. clavigera, 2,308 (40.4%) were O. montium, 838 (14.7%) were L. longiclavatum, and 379 isolates (6.6%) were morphologically intermediate between G. clavigera and L. longiclavatum. As described previously, MLST genotyping determined that the majority (90%) of the strains classified as “intermediate” were identified as L. longiclavatum [25, Electronic Supplementary Material 3] and had similar spatial and temporal distribution as L. longiclavatum. Based on this evidence, we grouped all intermediate strains with L. longiclavatum (n = 1,139, 19.9%) for subsequent analyses. Using these data, we identified significant landscape-level variation in relative abundance of fungal species (Table 2, Fig. 1). In particular, the abundance of both O. montium and G. clavigera decreased in northern landscapes, although the change in G. clavigera abundance was greater than O. montium. The decrease in G. clavigera abundance in the north was accompanied by an increase in L. longiclavatum.

Table 2.

Total number of galleries and species scored in each landscape and the relative abundance of each fungal species

	Period	Total Gall	Total Morph	Gc		Om		LI
				n	RA	n	RA	n	RA
North
FV	1	86	180	54	0.30	71	0.39	55	0.31
FV	2	306	654	201	0.31	237	0.36	216	0.33
TR	2	272	569	211	0.37	221	0.39	137	0.24
GP	1	175	341	110	0.32	124	0.36	107	0.31
GP	2	274	567	179	0.32	217	0.38	171	0.30
FC	1	60	129	41	0.32	49	0.38	39	0.30
FC	2	88	148	69	0.47	40	0.27	39	0.26
WK	1	148	329	116	0.35	132	0.40	81	0.25
WK	2	184	397	115	0.29	162	0.41	120	0.30
V	2	189	403	171	0.42	175	0.43	57	0.14
North totals		1,782	3,717	1,267		1,428		1,022
North average RA					0.35		0.38		0.27
South
G	2	176	356	165	0.46	161	0.45	30	0.08
KY	2	152	298	143	0.48	131	0.44	24	0.08
CA	1	102	188	98	0.52	82	0.44	8	0.04
CA	2	318	580	305	0.53	248	0.43	27	0.04
SW	2	203	392	190	0.48	185	0.47	17	0.04
CN	1	28	49	24	0.49	23	0.47	2	0.04
CN	2	70	113	67	0.59	39	0.35	7	0.06
CH	2	21	24	11	0.46	11	0.46	2	0.08
South totals		1,070	2,000	1,003		880		117
South average RA					0.50		0.44		0.06
Totals		2,852	5,717	2,270		2,308		1,139

Location and sampling period abbreviations as in Table 1

Gc, G. clavigera; Om, O. montium; Ll, L. longiclavatum; RA, relative abundance

Using PCA, we further explored this latitudinal trend (Fig. 2). The first PCA axis (PC1) was statistically significant and represented 92.15% of the variation in relative abundance of fungal species (Fig. 2). The small amount of variance captured by the second axis (PC2—7.41%) was not statistically significant and indicated that the ordination biplot should only be interpreted with regard to PC1. Fungal community structure was primarily driven by the relative abundance of L. longiclavatum, and this trend was strongly and significantly associated with increasing latitude, based on our post-hoc fitted vector of latitude values (R ² = 0.8159, p = 0.001; Fig. 2). In contrast, the relative abundance of G. clavigera, and to a lesser degree O. montium, was associated with elevation (R ² = 0.452, p = 0.001; Fig. 2). The northern and southern landscape groups were resolved by PC1 (Fig. 2), with the exception of V.bb and V.cc, two northern sites that cluster more closely with southern sites, rather than other northern sites. As hypothesized, L. longiclavatum became more abundant as latitude increased and G. clavigera decreased in abundance as latitude increased, although this latter trend appeared less pronounced and also appeared related to increased elevation in the southern region of the study area. O. montium did not correlate as strongly with latitude as L. longiclavatum and G. clavigera but was nonetheless associated with southern sample locations (right quadrants of ordination; Fig. 2. PCA also identified several unique sample sites. A single site in Crowsnest Pass in 2008 (CN.bb) showed unique composition relative to the rest of the sites (Fig. 3). This site had greater than expected relative dominance by G. clavigera and had a similar reduction in O. montium.

Figure 2.

Principle component biplot of proportional fungal composition across 50 sample sites in Alberta and British Columbia. Black text represents sample sites. Sample region (landscape—as in Fig. 1) is indicated by the capital letters to the left of the period in the text labels, while characters to the right of the period represent site IDs (collections of trees) within those regions. Double characters (e.g., “aa”) were sites collected in period 2, while single characters (e.g., “a”) were sites collected in period 1. Species proportions are represented by black vectors. Gray vectors represent fitted vectors of latitude (R ² = 0.816; p = 0.001) and elevation (R ² = 0.452; p = 0.001) that indicate the strength of correlation of these factors with the ordination. Italicized labels in the lower left and right quadrants of the ordination indicate directional association of sites with latitude. Gc, G. clavigera; Ll, L. longiclavatum; Om, O. montium

Figure 3.

Relative abundance of each species as a function of latitude. Each point represents the percentage of each species at a particular site calculated as a proportion of total number of isolates for each location. Straight lines are linear regression lines fit by least squares. Sample site labels as in Fig. 2. Gc, G. clavigera; Om, O. montium; Ll, L. longiclavatum

Rates of Change

Three mixed-effects regression models were built to describe relative abundance as a function of latitude and elevation for each species (Fig. 3; Table 3). Both G. clavigera and L. longiclavatum were strongly affected by changes in latitude; G. clavigera abundance decreased with latitude and, conversely, L. longiclavatum abundance increased with latitude. O. montium was also affected by changes in latitude, although this relationship was not as strong as was observed in the other species (Table 3). Relative abundance of G. clavigera was influenced by the interaction between latitude and elevation, although this effect was weak relative to that of latitude (Table 3). Neither elevation alone nor in combination with latitude helped explain variation in the relative abundance of O. montium or L. longiclavatum.

Table 3.

Summary of mixed-effect regression models describing relative abundance of each morphotype as a function of latitude

Model	Species	LogLik	Parameter	Value	Std. error	F	p
1	Gc	63.208	Intercept	0.389	0.015	697.875	0.000
			Latitude	−0.079	0.014	30.753	0.000
			Elevation	0.002	0.014	0.022	0.884
			Lat. × Elev.	−0.030	0.015	4.156	0.049
2	Om	69.500	Intercept	0.411	0.014	865.466	0.000
			Latitude	0.028	0.013	4.229	0.047
			Elevation	0.003	0.013	0.046	0.832
			Lat. × Elev.	0.011	0.014	0.666	0.420
3	LI	71.595	Intercept	0.198	0.015	183.331	0.000
			Latitude	0.104	0.014	55.168	0.000
			Elevation	−0.001	0.013	0.003	0.956
			Lat. × Elev.	0.017	0.014	1.509	0.227

In all models, landscape ID (see Table 1) was used as a random effect, and latitude and elevation were used as fixed effects

Gc, G. clavigera; Om, O. montium; Ll, L. longiclavatum

Three mixed-effect ANCOVA tests were used to assess the differences between the slopes of the modeled relationships between species abundance and latitude. The absolute rates of change in G. clavigera and L. longiclavatum in response to latitude were not significantly different based on examination of the interaction term between species and latitude (ANCOVA; F = 3.48, p = 0.065) and suggested symmetrical replacement along the sampled latitudinal gradient. The slopes of the models for G. clavigera and O. montium were different (ANCOVA; F = 34.04; p < 0.001), as were those for L. longiclavatum and O. montium (ANCOVA; F = 46.18, p < 0.001). We did not examine differences in each species’ response to elevation because of the lack of a strong and consistent response to elevation for all species, and the strong negative correlation between latitude and elevation (r=−0.74) which indicated that the two covariates represent a very similar gradient.

Temporal Variation

Some differences in relative abundance were observed between years (Fig. 4). In general, more isolates were identified as G. clavigera in period 2 than in period 1, and similarly fewer isolates were identified as L. longiclavatum. No change was observed in O. montium between years. Despite these trends, the effect of sampling period on abundance was not significant for either G. clavigera (ANCOVA; F = 0.699, p = 0.407) or L. longiclavatum (ANCOVA; F = 0.47, p = 0.4933).

Figure 4.

Boxplots illustrating differences in relative abundance for each species between sampling periods

Species Coexistence

The relative proportion of species associations within MPB galleries varied spatially (Table 4; Fig. 5). Of the galleries surveyed, nearly all contained at least one ophiostomatoid fungal species (99.97%), with the majority containing two species (Table 4, Fig. 5). The most common association occurred between G. clavigera and O. montium (G. clavigera–O. montium, 46%; Table 4, Fig. 5). Cypress Hills was the exception where the majority of galleries contained only a single species (G. clavigera; Fig. 5).

Table 4.

Summary of observed species combinations within MPB galleries

Number of morphotypes within a gallery
	Total galleries	1						2						3		0
		Gc		Om		Ll		Gc–Om		Gc–Ll		Om–Ll		Gc–Om–Ll
		n	RA	n	RA	n	RA	n	RA	n	RA	n	RA	n	RA	n	RA
Northa	1,782	136	0.0763	82	0.0460	54	0.0303	564	0.316	130	0.0730	373	0.209	437	0.245	6	0.003367
Southb	1,070	163	0.152	6	0.00561	42	0.0393	745	0.696	18	0.0168	16	0.0150	77	0.0720	3	0.00280
Total	2,852	299	0.105	88	0.0309	96	0.0337	1,309	0.459	148	0.0519	389	0.136	514	0.180	9	0.003156

Landscape abbreviations as in Table 1

Gc, G. clavigera; Om, O. montium; Ll, L. longiclavatum; RP, relative abundance

^aNorth: FV, TR, GP, FC, WK, V

^bSouth: G, KY, CA, SW, CN, CH

Figure 5.

Relative proportion of observed fungal species associations within MPB galleries, summarized for each of 12 landscapes. Inset shows overall global species associations: Gc, G. clavigera; Om, O. montium; Ll, L. longiclavatum. Landscape labels as in Fig. 1

Within the entire study area, the frequencies of the three possible pair-wise combinations were different from each other (Χ ² = 610.69, df = 2, p < 0.001) given expected frequencies based on species abundances. Similar results were found for both northern (Χ ² = 220.13, df = 3, p < 0.001) and southern regions (Χ ² = 224.26, df = 2, p < 0.001). Almost all paired comparisons were also significant. The one exception to this was in the southern region where the frequency of the G. clavigera–L. longiclavatum combination was not different than that of O. montium–L. longiclavatum (2.3% vs. 2%; Χ ² = 0.03, df = 1, p = 0.86). However, both combinations were different from expected given individual abundances. In fact, we found that the frequency of each individual combination was significantly different than expected (all Χ ² > 30, p < 0.001) given the relative abundances of each species, with the exception of the O. montium–L. longiclavatum pairing in the northern region (Χ ² = 1.96, df = 2, p = 0.16).

Similar to the results described above, we also found that the proportions of each pair-wise combination were different between northern and southern regions (all Χ ² > 100, p < 0.001).

In sites belonging to the southern group (CA, CH, CN, G, KY, SW) where L. longiclavatum was relatively rare (abundance <20%), G. clavigera–O. montium is by far the most common species combination in galleries (Fig. 5). In the northern group of sites (FC, FV, GP, TR, V, WK) where L. longiclavatum was more common (abundance >20%), a different species coexistence pattern was observed. The association between G. clavigera–O. montium was less common (Χ ² = 195, df = 2, p < 0.001), while the associations that included L. longiclavatum significantly increased in frequency, including O. montium–L. longiclavatum (Χ ² = 52.05, df = 2, p < 0.001) and the combination of all three species (G. clavigera–O. montium–L. longiclavatum). Although G. clavigera–L. longiclavatum also increased in frequency in the northern region (1.7% vs. 7.3%; Χ ² = 192.24, df = 2, p < 0.001), it remained the rarest combination even with increased L. longiclavatum abundance.

Discussion

We identified and described spatial and temporal variation in fungal symbiont abundance and community composition in MPB galleries at the leading edge of an outbreak. Specifically, we identified spatial variation in the relative abundance of all three species and found that the degree of spatial variation differed between species. Changes in relative abundance of G. clavigera and L. longiclavatum were strongly determined by latitude, while changes in O. montium were less apparent. Elevation did no account for additional variation in fungal abundance in O. montium and L. longiclavatum but did weakly influence the abundance of G. clavigera in combination with latitude. We used latitude and elevation as simple proxies for climatic conditions, similar to what has been done previously in other studies of fungal diversity [e.g., 35–37]. Although high elevation and low latitude have potentially different temperature-related consequences, we were unable to fully examine these factors independently due to their correlated nature, as well as the nature of our sampling scheme that fell along this gradient.

Fungal Abundances

When we compared the observed variation in fungal abundance with previously published accounts, a landscape-scale pattern emerged. In earlier studies, the majority of work occurred in southern MPB populations where L. longiclavatum was rarely encountered [12, 18]. Our results, in congruence with Rice and Langor [18], indicate that L. longiclavatum becomes more abundant in northern sites (Figs. 2 and 3). By comparing the slopes of the relative abundance of the three species, we observed a gradual change in abundance with increasing latitude in this species. Furthermore, a symmetrical and opposite rate of change was also observed in G. clavigera. The symmetry of these two slopes (Fig. 3) suggests that G. clavigera is being replaced by L. longiclavatum as latitude increases, in turn suggesting competitive exclusion of one species by the other. While both G. clavigera and O. montium decrease in abundance with increasing latitude, the rate of change in O. montium was less pronounced. This finding was contrary to our initial expectations. Given that previous work has shown O. montium to be temperature sensitive in Montana and Idaho [7] and with a higher optimal growth temperature and slower growth at cool temperatures than G. clavigera [19, 20], we expected that O. montium would show a similar or greater rate of decreasing abundance with increasing latitude than G. clavigera. However, our findings do support other observations that in northern regions O. montium demonstrates variability in cold tolerance and may be more cold tolerant than initially thought [18].

Fungal Community Composition

The symmetrical rates of change and apparent replacement of G. clavigera by L. longiclavatum at northern latitudes suggest that processes of competitive exclusion are influencing patterns of fungal community composition. This is further supported by the observation that G. clavigera and L. longiclavatum are rarely paired together within a gallery (Table 4), while the combination of G. clavigera and O. montium, and O. montium and L. longiclavatum are more common (Table 4). Furthermore, in almost all cases, the relative frequencies of the possible pair-wise combinations are different from what is expected given the raw abundances of the species. This indicates non-random associations between fungal symbionts that vary spatially. Interestingly, the one exception to this pattern is the O. montium–L. longiclavatum combination in the north, the frequency of which was proportional to the frequency of each individual species.

Phylogenetically, L. longiclavatum and G. clavigera are closely related while O. montium is more distantly related [38, 39]. G. clavigera and L. longiclavatum are also morphologically similar and have similar physiological requirements, such as similar growth temperature optima [12, 13, 19, 40], thereby increasing the potential competitive interactions between these two species. Conversely, fine-scale differences in resource use may reduce competition between O. montium and G. clavigera [21]. Given these traits, G. clavigera and L. longiclavatum may be unable to coexist due to significant niche overlap, while O. montium is dissimilar enough to allow coexistence with either species, although in vitro competition experiments to examine all of these fungal combinations have not yet been conducted. Interestingly, while G. clavigera and L. longiclavatum rarely occur together as a pair, all three species together are able to coexist (Table 4). We hypothesize that the addition of the third species, O. montium, may create a niche space that allows all three species to coexist, a natural example of a “rock-paper-scissors” means of coexistence [41]. In a “rock-paper-scissors” scenario, competition between pairs of species results in one species out-competing the other. However, in this three-species system, it is possible that local competition creates additional niche space that, in combination with dispersal and repeated invasions, facilitates coexistence and the maintenance of fungal diversity [41]. Functionally, the maintenance of this fungal diversity could be essential to persistence and stability of mountain pine beetle populations across a broad range of climatic conditions. In vitro growth experiments that examine the interactions between different fungal symbionts, similar to work previously conducted on G. clavigera and O. montium [21], would be an ideal approach to test the hypothesis of a “rock-paper-scissors” means of coexistence and to further explore patterns of competition and coexistence among these fungi.

Temporal Variation

Although we did not find significant differences in species abundances between years, we did observe some interesting temporal trends in G. clavigera and L. longiclavatum (Fig. 4). We also identified unexplained variation in fungal abundance at some individual sites (i.e., CN.bb; Fig. 3). Variation between sample periods and among sites in our data may also be a product of weather, dispersal patterns, or local environmental factors (e.g., temperature or elevation). Based on survey data, we know that some populations, particularly those in northeastern BC and northwestern AB may have originated from long-distance dispersal events [6]. These migrant populations may be associated with different fungal communities, impacting year-to-year differences in fungal composition at sites experiencing repeated long-distance colonization. Uncertainty in the relative roles of these different factors highlights the need for further research into beetle movement and patterns of gene flow in both the beetle and its fungal associates as a function of spatial and temporal variation. Furthermore, although previous work observed changes in fungal abundance over time in a single season [17, 40], our results indicate that it may be useful to track these changes over longer time periods. This will be particularly important as MPB populations expand into novel environments such as the jack pine forests in northern Alberta, or as they shift from epidemic to endemic levels.

Potential Sources of Bias

By standardizing our sampling methodologies (e.g., cool period sampling, room temperature incubation), we may have introduced systematic bias into our assessment of fungal community structure, for example, favoring faster-growing and prolifically sporulating fungal species over slower-growing species, or characterizing the fungal community composition associated with cool weather as opposed to warm weather conditions. With this potential bias in mind, it is interesting to note that the less-prolific sporulating species (O. montium) is quite abundant and shows less response to latitude than either of the two rapidly sporulating fungal species (G. clavigera and L. longiclavatum). Given this pattern, we are confident that the patterns observed reflect actual trends in community structure rather than an artifact of our collection and isolation practices.

By contrasting the morphotyping results with the MLST genotypes of a subset of isolates, we identified additional potential biases in our surveys that could also affect other ecologically based studies of these fungi. First, the vast majority of strains identified by morphological characteristics as “intermediate” between L. longiclavatum and G. clavigera were actually L. longiclavatum. Here, the availability of molecular data provided objective justification for their inclusion with L. longiclavatum count data in subsequent analyses. Second, MLST data suggest that the actual fungal proportions associated with MPB are likely overestimated for G. clavigera and O. montium and underestimated for L. longiclavatum proportions due to morphological misdiagnoses. However, it is likely that these biases would augment the patterns observed in the morphologically diagnosed data rather than diminish them. Third, the two additional fungal associates, G. aurea and L. terebrantis, identified using MLST data were not identified morphologically but appear to form a very small proportion of the overall fungal symbiont fauna associated with MPB. Their inclusion, had they been reliably distinguishable by morphological characteristics likely would not affect our inferences regarding the relationships between geographical location and fungal community composition. Together, these observations point to the utility of applying DNA-based identification techniques [25, 42–44] to the mixed-species environmental cultures that were obtained to confirm species identifications and to test for cryptic species assemblages.

Conclusions

We identified significant biogeographic patterns of community composition in the major mountain pine beetle associated fungal symbionts. The observed patterns of species coexistence and competitive exclusion among fungi suggest that complex ecological processes are controlling community structure [45]. As in other bark beetle systems, variation in fungal symbiont associations [9, references therein] has been linked to environmental factors and substrate variability [7, 46–49]. Dynamics and interactions between co-occurring bark beetle symbionts have also been explored [46, 50–52]. This study provides one of the first large-scale surveys of symbiont composition patterns in natural MPB populations, giving insight to landscape-level processes impacting symbiont community dynamics. Understanding the biotic and abiotic factors that lead to symbiont community variability over time and space is imperative as the symbiont community can impact beetle colonization success and population dynamics [9, 48, 53].

To further understand the mechanisms behind the patterns of variation in fungal symbionts, it will be important to link fungal abundance and community composition to additional environmental features (e.g., fungal “habitat”) and to examine the persistence of these trends throughout the life cycle of the beetle. Furthermore, explicit quantification of the interactions between the three primary fungal symbionts through growth experiments on artificial media, particularly under varying temperature regimes, are required to determine the mechanisms that underpin the observed biogeographic patterns of MPB fungal community changes. Variation in fungal symbiont assemblages across a range of environmental conditions represents an important element of MPB functional diversity that, in combination with intraspecific variation within the symbionts and host, will be important to understand the success of MPB attacks in novel habitats and to predict future risk of outbreak.

Electronic supplementary material

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