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Keywords:

  • Abies lasiocarpa;
  • Juncus spp.;
  • plant establishment;
  • revegetation;
  • Saxifraga spp

Abstract

  1. Top of page
  2. Abstract
  3. Introduction
  4. Materials and methods
  5. Results
  6. Discussion
  7. Acknowledgements
  8. References

1 We characterized safe sites for individuals of five early colonizers (Abies lasiocarpa, Juncus drummondii, J. mertensianus, Saxifraga ferruginea, S. tolmiei) that had survived at least one growing season on the recently deglaciated forefront of the Lyman Glacier in the North Cascade Mountains, Washington, USA.

2 Sites with concave surfaces, coarse surface substrate and in the vicinity of large rocks were more likely to be colonized by pioneering plant species.

3 We speculate that the distribution of plants is determined by the presence of sites that facilitate seed trapping and protect seeds and seedlings from desiccation.

4 The data identify the abiotic factors that determine initial recruitment and spatial distribution of plants. Such controls precede biotic interactions in this primary successional sere.


Introduction

  1. Top of page
  2. Abstract
  3. Introduction
  4. Materials and methods
  5. Results
  6. Discussion
  7. Acknowledgements
  8. References

Most studies on succession and successional mechanisms have concentrated either on biotic interactions (Connell & Slatyer 1977; Pickett et al. 1987; Matthews 1992; Chapin et al. 1994; Callaway 1995; Holmgren et al. 1997; Jumpponen et al. 1998) or on the ways in which abiotic changes are correlated with changes in plant communities (Crocker & Major 1955; Viereck 1966; Matthews & Whittaker 1987; Matthews 1992; Vetaas 1997; Frenot et al. 1998; Jumpponen et al. 1998). While both biotic and abiotic factors are critical at various stages in the development of plant communities, the early dynamics in primary successional habitats are under strictly abiotic control (Houle 1997). Such development of vegetation on newly formed or exposed substrate proceeds on raw parent material, rather than a developed or modified soil, and this is usually characterized by low nitrogen and organic matter (Glenn-Lewin et al. 1992; Matthews 1992). Only as plants establish and modify their physical environment, do intra- and interspecific interactions between individual plants become more significant (Houle 1997). The role of abiotic factors in primary successional environments is also seen in the prevalence of wind-dispersed propagules, whose distribution is controlled by environmental factors after the seeds have been released from the seed source (Bigwood & Inouye 1988).

Although subtle differences in seed distribution and soil surface properties dramatically affect both establishment and survival of plants (Harper et al. 1965; Sheldon 1974; Hamrick & Lee 1987; Huenneke & Sharitz 1990), recruitment in primary successional systems has been little studied. Harper et al. (1961) proposed the term ‘safe sites’ to describe microsites suitable for germination and establishment. The importance of such sites and the abiotic factors characterizing them have been emphasized in primary succession (Matthews & Whittaker 1987; Svoboda & Henry 1987; Whittaker 1991; Frenot et al. 1998) but they have rarely been studied, despite the fact that such habitats are frequently characterized by harsh environmental conditions due to drought and/or exposure (Matthews 1992; Chapin 1993) that may induce early mortality of germinants (Chapin & Bliss 1989). The mechanisms of primary and secondary seed dispersal must also be considered as they govern the supply of seeds to safe sites.

The main objective of this study was to identify the characteristic microenvironment at safe sites suitable for initial plant colonization on the recently deglaciated forefront of the Lyman Glacier in the North Cascade Mountains, Washington, USA. The various factors that may govern seed dispersal and plant establishment were evaluated indirectly by characterizing the microenvironment around newly established plants in situ. Successful establishment depends on a site promoting the trapping of seeds or vegetative propagules, but although the existing seed bank is an essential component in plant recruitment and the resulting community, its composition may not be a good predictor of the distribution of plants able to survive and reproduce in that site (van der Valk 1992). Seed accumulation is only the first step towards successful seedling recruitment; the site must also provide conditions that support both germination and survival of some of the species present in the soil seed bank. Furthermore, one substrate or site may support high germination, while another may support high survivorship (Reader & Buck 1986; Huenneke & Sharitz 1990). In the initial stages of primary succession, the plants that actually establish must show success in all of seed trapping, seed germination and seedling establishment. We therefore located plants that had survived through at least one growing season on otherwise non-vegetated primary successional terrain close to the glacier terminus, and described their microsites to derive indicators that integrate all the requirements of a safe site.

Materials and methods

  1. Top of page
  2. Abstract
  3. Introduction
  4. Materials and methods
  5. Results
  6. Discussion
  7. Acknowledgements
  8. References

Study site

Lyman Glacier (48°10′N, 120°53′W; 1800 m above sea level) is retreating and over the past century has exposed a forefront extending 1100 m but with a drop in elevation of only about 60 m and without distinctive recessional moraines. The glacier and its forefront occupy a cirque and a north–south orientated, U-shaped valley bounded by cliffs that rise up to 600 m above the valley floor. The parent material of the forefront is a heterogeneous glacial till ranging from clay-sized particles to boulders intermingled with deposits of glacial–fluvial sediments (for a detailed description see Ca´zares 1992 and Jumpponen et al. 1998).

The vegetation on ridges and benches in areas adjacent to the forefront is in the ecotone between the upper parkland subzones of the Abies lasiocarpa zone and Tsuga mertensiana zone of the North Cascade Range (Franklin & Dyrness 1973). Succession on the glacier forefront can be divided into four vegetational phases (Jumpponen et al. 1998): (i) a barren phase less than 20 years since exposure that lies closest to the glacier; (ii) a 20–30-year-old phase that is dominated by scattered individuals or small patches of the early seral species Juncus drummondii, J. mertensianus, Luzula piperi, Saxifraga ferruginea and S. tolmiei[the ‘rawmark’ community of Franklin & Dyrness (1973)]; (iii) a phase approximately 30–70 years old that is characterized by scattered shrubs (principally the willows Salix phylicifolia var. planifolia and Salix commutata) and occasional Pinaceae mixed with rawmark or low herbaceous communities (Franklin & Dyrness 1973) dominated by species of Cyperaceae, Juncaceae, Onagraceae, Saxifragaceae and Scrophulariaceae, with scattered individuals of other families; and (iv) a phase approximately 70–100 years old that is characterized by transition from low herbaceous to early stages of the heath shrub and lush meadow parkland communities containing individuals of A. lasiocarpa, Larix lyallii and T. mertensiana among patches dominated by several members of Ericaceae. Data for the current study were collected from an area that extends approximately 250 m from the current glacier terminus, which encompasses phase 1 and the transition between phases 1 and 2. We estimated that less than 1% of this area was vegetated, and what vegetation there was consisted of small, isolated individuals of a variety of species (Table 1).

Table 1.  Plant species present and numbers recorded within the first 250 m from the Lyman Glacier terminus. Nomenclature follows Hitchcock & Cronquist (1973). Species with fewer than 20 observations were omitted from the analyses
FamilySpeciesObservations
PinaceaeAbies lasiocarpa (Hook.) Nutt. 43
Pinus albicaulis Engelm.<20 
Pinus contorta Dougl.<20 
CompositaeAntennaria lanata (Hook) Greene<20
Hieracium gracile Hook.<20 
EricaceaePhyllodoce empetriformis (Sw.) D. Don<20
OnagraceaeEpilobium alpinum L.<20
Epilobium latifolium L.<20 
JuncaceaeJuncus drummondii E. Meyer 
Juncus mertensianus Bong. 59 
Luzula piperi (Cov.) Jones<20 
RosaceaeLuetkia pectinata (Pursh) Kuntze.<20
CaryophyllaceaeSagina saginoides (L.) Britt.<20
SaxifragaceaeSaxifraga ferruginea Grah. 
Saxifraga tolmiei T. & G. 41 

Sampling and data collection

To ensure correct identification of plant species other than A. lasiocarpa and the two distinctive Saxifraga spp., only plants in flower were recorded. Approximately 600 individual plants were located in the area of initial colonization (Table 1) and identified. A 10 cm × 10 cm area centred on each plant was defined as a safe site and this was characterized using the following parameters: distance from the glacier terminus, distance from a rock >20 cm in diameter, general topology (elevated, depressed or flat), position (slope, top or bottom), depth with respect to a imaginary 1-m2 plane suspended from the highest surrounding points, surface contour (concave, convex, plateau), orientation of exposure (north, south, east, west), proportion of the surface covered by substrate particles <2 mm in diameter, and proportion of the surface covered by substrate particles >2 mm but <2 cm in diameter. A similar area was marked out 50 cm south of the vegetated site. If this area was non-vegetated, it was designated as a control site and the same variables were recorded. If this site was vegetated or plant recruitment was considered unlikely (e.g. if the area fell on bare rock or in standing water) an alternative control site was sought at a position obtained by 90° clockwise rotation. A control site was available within 50 cm of each safe site.

Statistical analyses

Of the 15 species recorded, only five had more than 20 records of occurrence (Table 1) and these were analysed by logistic regression: sites with a plant represented an event, while the non-vegetated controls represented a non-event. The plant species were sampled at an equal frequency with their neighbouring non-vegetated control sites. As a result, species could not be used as a main effect but could only be incorporated into the interaction terms. Due to the overwhelming numbers of potential interaction terms (species × environmental variable), the species were analysed separately. When a number of the measured variables was found to be correlated, all but one were omitted and four variables (Table 2) were thus selected for final analyses. A saturated model with two continuous variables (distance to a rock and proportion of coarse substrate), two categorical variables (surface contour, with plateau as the reference level, and topology, with position on a flat surface as the reference level), and all two–way interactions was fit on the Bernoulli-distributed, binary, presence/ absence data. Only the main effects and two-way interactions were included in the saturated model because of the vast number of potential interaction terms and the difficulties of interpretation of multi-level interactions. Saturated models were first compared to additive models with no interaction terms by drop-in-deviance tests (Ramsey & Shafer 1996). If the interactions were not significant at α = 0.05, only additive models were studied further and an additive model with the lowest value of Q (McCullagh & Nelder 1989) was selected [Q = D + 2qd, where D = model deviance, q = number of explanatory parameters in the model, d = scaling parameter (due to Bernoulli distribution, here always 1)]. If drop-in-deviance tests showed saturated models significantly more informative at α = 0.05 than the additive models, the ‘best model’ with interaction terms was again selected by minimizing the value of Q. Data were analysed in SAS using the GENMOD procedure (SAS 1997).

Table 2.  Description of the variables used in the final logistic regression analyses to characterize the safe sites for the early establishing plants in the primary successional habitat on the Lyman Glacier forefront. Parameter names used in Table 3 are displayed in parentheses
VariableTypeDescription
1 Distance from a rock (Distrock)ContinuousDistance from the edge of a rock >20 cm in diameter to the site centre
2 Topology (Topology)CategoricalRelative topology of site compared to topography of surrounding area within 1 m2: elevated, depressed, or flat (reference level)
3 Surface contour (Surface)CategoricalSurface shape within the 10 × 10 cm site: concave, convex or plateau (reference level)
4 Proportion of coarse substrate (Coarse)ContinuousPercentage of site covered with particles >2 mm but <2 cm in diameter. Pebbles >2 cm in diameter were not considered as substrate

Results

  1. Top of page
  2. Abstract
  3. Introduction
  4. Materials and methods
  5. Results
  6. Discussion
  7. Acknowledgements
  8. References

The best logistic regression models describing safe sites for each five major plant species in a primary successional system on a retreating glacier forefront are displayed in Table 3.

Table 3.  Logistic regression models characterizing the safe sites for the five plant species recorded in the primary successional site on the Lyman Glacier forefront. Odds ratio indicates the proportion of events compared to non-events (ratio between vegetated sites and non-vegetated sites under the condition defined by the parameter)
ParameterOdds-ratio95% confidence intervalsP (χ2, d.f. = 1)*P (χ2, d.f. = 1)*
LowerUpper
  • *

    Type 1 analysis; significance of the parameter as sole explainer of variation; set of previous parameters does not affect the parameter significance.

  • Type 3 analysis; significance of the parameter after accounting for all the previous parameters in the model.

Saxifraga ferruginea
Intercept0.07350.0358 0.14560.0001
Distrock (P = 0.0084, χ2, d.f. = 1)†0.98280.9693 0.99560.0108
Topology (P = 0.0001, χ2, d.f. = 2)† 
Depressed1.03210.6163 1.72860.9041
Elevated0.39670.2288 0.68610.0009
Surface (P = 0.0001, χ2, d.f. = 2)† 
Concave4.84233.0851 7.70140.0001
Convex1.11810.6792 1.84150.6605
Coarse (P = 0.0001, χ2, d.f. = 1)†1.02621.0192 1.03380.0001
Deviance = 828.1043
Q = 842.1043
Juncus drummondii
Intercept0.10020.022 0.41190.0020
Distrock (P = 0.0001, χ2, d.f. = 1)†0.77830.4119 0.93370.0203
Topology (P = 0.9708, χ2, d.f. = 2)† 
Depressed1.11640.6127 2.89820.8186
Elevated1.12750.3583 3.610.8380
Surface (P = 0.0001, χ2, d.f. = 2)† 
Concave6.22273.251112.45470.0001 
Convex1.14430.4934 2.57770.7476
Coarse (P = 0.2035, χ2, d.f. = 2)b1.0090.995 1.02530.2335
Distrock × topology (P = 0.0153, χ2, d.f. = 2)†  
Distrock × depressed1.0130.9456 1.11960.7543
Distrock × elevated0.76860.5655 0.96020.0479
Distrock × Coarse (P = 0.0187, χ2, d.f. = 1)†1.00221.0003 1.00470.0454
Deviance = 378.9326
Q = 398.9326
Abies lasiocarpa
Intercept0.00920.0013 0.04940.0001
Distrock (P = 0.0001, χ2, d.f. = 1)†0.91430.8553 0.96140.0024
Topology (P = 0.0901, χ2, d.f. = 2)† 
Depressed1.87910.5399 7.57540.3376
Elevated0.72550.1802 3.20430.6553
Surface (P = 0.0001, χ2, d.f. = 2)† 
Concave5.94172.426916.42990.0002 
Convex0.55320.1131 2.12760.4138
Coarse (P = 0.0007, χ2, d.f. = 1)†1.02631.0104 1.04500.0023
Deviance = 207.7984
Q = 221.7984
Juncus mertensianus
Intercept0.00820.0015 0.03690.0001
Distrock (P = 0.0011, χ2, d.f. = 1)†0.94980.9125 0.98160.0054
Topology (P = 0.0028, χ2, d.f. = 2)† 
Depressed2.89941.0341 9.4830.0550
Elevated0.82510.2428 3.03890.7615
Surface (P = 0.0001, χ2, d.f. = 2)† 
Concave4.01771.9568 8.67550.0002
Convex0.44540.1184 1.36790.1847
Coarse (P = 0.0001, χ2, d.f. = 1)†1.02881.0145 1.04530.0002
Deviance = 269.9394
Q = 283.9394
ParameterOdds-ratio95% confidence intervalsP (χ2, d.f. = 1)*P (χ2, d.f. = 1)*
LowerUpper
Saxifraga tolmiei
Intercept0.01470.0018 0.09160.0001
Distrock (P = 0.0002, χ2, d.f. = 1)0.81460.0916 0.99730.1748
Topology (P = 0.1960, χ2, d.f. = 2) 
Depressed2.87050.510914.56470.1702 
Elevated1.26780.2488 7.16420.7770
Surface (P = 0.8089, χ2, d.f. = 2) 
Concave1.41540.4659 4.40440.5426
Convex1.02190.1457 8.15070.9824
Coarse (P = 0.0010, χ2, d.f. = 1)1.02531.0095 1.04400.0033
Distrock × surface (P = 0.0123, χ2, d.f. = 2)  
Distrock × concave1.21191.0227 1.58630.0797
Distrock × convex0.69240.1692 1.28340.4175
Distrock × topology (P = 0.8543, χ2, d.f. = 2)  
Distrock × depressed0.99910.7964 1.6010.9950
Distrock × elevated0.96280.7179 1.55710.8119
Deviance = 206.9117
Q = 228.9117

Three species (A. lasiocarpa, J. mertensianus and S. ferruginea) were most likely to occur close to large (>20 cm) rocks. An increase in the distance from such a rock decreased the recruitment probability of these species, as indicated by odds ratios significantly less than 1 (Table 3). For J. drummondii increase in the distance from a rock substantially decreased the probability for recruitment in elevated positions (which are unlikely locations for recruitment, except close to large rocks), while no such effect was visible in depressed positions. Other parameters, such as coarse substrate for J. drummondii or concave surfaces for S. tolmiei, also facilitated recruitment, and when these were present the rock effect was minimal or non-existent. For example, coarse substrate interacted with distance from rocks for J. drummondii: the presence of coarse substrate overrode the effects of being distant from a substantial obstruction and proximity to a rock compensated for too little coarse substrate.

Although included in the models for all species, topology did not significantly affect recruitment of either A. lasiocarpa or S. tolmiei (type 3 analysis P= 0.0901 and 0.1960, respectively). Recruitment of J. mertensianus may be more likely in the depressions than in flat positions (type 1 analysis P= 0.0550), whereas S. ferruginea recruitment was substantially less likely in the elevated positions than on flats or depressions that did not differ from each other (type 1 analysis P= 0.0009; Table 3). For J. drummondii, topology interacted with distance to large rocks as described above.

Surface contour was a significant parameter in explaining the presence of most species. While convex and plateau surfaces did not differ, concave surfaces had substantially higher odds for recruitment of A. lasiocarpa, J. drummondii, J. mertensianus and S. ferruginea (Table 3). For S. tolmiei, surface characteristics interacted with distance from large rocks and no clear conclusions were possible, although it appears that concave surfaces were less advantageous when located near a substantial physical obstruction. However, this S. tolmiei data set contained the fewest observations and therefore might be less reliable.

Increase in coarse substrate also usually enhanced plant recruitment. An increase in surface coverage by coarse substrate (>2 mm in diameter) resulted in an increase in recruitment probability for A. lasiocarpa, J. mertensianus, S. ferruginea and S. tolmiei. For J. drummondii, however, as described above, substrate interacted with distance from substantial rocks. The pattern was similar to the interaction of surface characteristics with distance to rocks for S. tolmiei (Table 3).

Discussion

  1. Top of page
  2. Abstract
  3. Introduction
  4. Materials and methods
  5. Results
  6. Discussion
  7. Acknowledgements
  8. References

The data presented here indicate that the spatial distribution of the first plants to colonize a primary successional glacier forefront is not random. Successful establishment and survival of plant individuals occurs only in safe sites and these can be characterized simply by their physical attributes.

Concave surfaces had substantially greater overall plant recruitment than convex or plateau surfaces. The five species analysed depend primarily on wind dispersal. Spatial variation in seed rain and the non-uniform distribution of sites where seeds become trapped result in a soil seed bank with a strongly clustered spatial distribution (Ryvarden 1971; Rabinowitz & Rapp 1980; Reichman 1984; Price & Reichman 1987; Bigwood & Inouye 1988). Small depressions and concave surfaces provide a ‘wind shadow’ where surface wind velocities are lower and surface water flow may slow or stop, leading to substantial seed accumulation as a result of horizontal seed movement (Reichman 1984). Depressions appear to be effective collectors of seeds undergoing either primary and secondary dispersal (Reichman 1984; Matlack 1989).

Besides trapping seeds from transient populations, shallow depressions may also provide greater moisture than the surrounding soils and thus enhance seed germination, particularly in environments where surface desiccation may be a major factor (Watt 1919). Early successional sites are characterized by intense radiation at the soil surface, which results in extreme fluctuations in soil temperature and rapid drying of surface soils (Chapin 1993). The importance of protection against water loss and desiccation has been emphasized for successful germination and establishment (Harper et al. 1965; Sheldon 1974; Hamrick & Lee 1987). Drought may, indeed, be the major cause of seedling mortality during the first year after germination in primary succession (Chapin & Bliss 1989). Seed trapping that leads to the clustering of seeds in small depressions or other locations where germination and survival are likely to be enhanced would result in a strong effect similar to that observed here. In a controlled study of microsites, in which heterogeneity was created experimentally, Harper et al. (1965) concluded that the majority of seedlings of two Plantago spp. emerged in depressions or near obstructions. It is likely that the promotion of germination will be more important since the conditions for plant survival and growth are generally less restrictive than those for germination. Provided that the emerging radicle is able to penetrate the soil surface, the likelihood of subsequent establishment is high (Sheldon 1974).

Plant occurrence was generally higher near large rocks, especially in locations where occurrence was otherwise unlikely. Livingston (1972) pointed out that Juniperus communis established more frequently near rocks in New England pastures and suggested that this might be a result of faecal deposition of seeds by robins resting on rocks after feeding on juniper berries, as well as to greater moisture levels due to a ‘microwatershed’ created by the rocks. Fowler (1986, 1988) similarly observed increased survival and growth near rocks and interpreted this to result mainly from reduced evaporation, but did not acknowledge the ‘microwatershed’ effect. We assume both to be important at our study site as extended periods of drought may occur annually in the glacier forefront and water retention is poor due to low organic matter content. Furthermore, rocks may create points for mountain dew to accumulate and thus further improve moisture conditions in the absence of precipitation. We have also observed on several occasions that snow adjacent to elevated rocks melts earlier, resulting in a lengthening of the short growing season at the Lyman Glacier forefront. The rock effect was, however, minimal or non-existent in the presence of other recruitment-facilitating parameters (coarse substrate, for J. drummondii; concave surfaces, for S. tolmiei), suggesting that the effect of rocks was similarly mediated via enhanced seed trapping and burial.

There are several likely factors involved in the greater occurrence of plants with greater amounts of coarse substrate. Like the small-scale depressions of the concave surfaces, coarse substrate contains seed trapping cavities between the particles. Coarse substrate also allows partial burial between the particles, improving the moisture retention around the seed and increasing the likelihood of successful germination. Surface water flow would move small seeds into the minute cavities and cracks in the surface and further percolate through the surface substrate with vertical flow (Bigwood & Inouye 1988). The protection offered by the cavities and the associated seed burial are essential for seeds to remain viable (Enright & Lamont 1989). Hamrick & Lee (1987) concluded that optimal conditions for successful establishment and survival were provided by small irregularities in the soil surface, particularly in areas prone to desiccation. Such burial may ensure that seeds remain viable but dormant until conditions are favourable for successful germination (Stamp 1989). Although seed predation was not measured directly, seed burial further reduces the likelihood of seed discovery by predators (Enright & Lamont 1989). Coarse substrate may also increase the likelihood of radicle penetration and seed anchorage because smooth and compacted surfaces provide few possibilities for successful penetration of the surface by the emerging radicle (Sheldon 1974). The substrate at the glacier forefront is mainly glaciofluvial silt intermingled with some coarser fragments. When desiccated, the silt frequently forms cemented crusts, precluding seed trapping and radicle penetration. Finally, needle ice formation occurs on the forefront in autumn if hard frost precedes a snow cover, and frost heaving is then a hazard to small plants. We observed that the needle ice formed mostly on silt surfaces but not where pebbles or gravel provided a surface mulch.

Topology had no significant effect on A. lasiocarpa, J. drummondii or S. tolmiei recruitment, although S. ferruginea recruitment was less likely in the elevated positions. Plant occurrence was therefore less dependent on topography relative to the surroundings than on parameters describing the microsite itself.

Although our design allowed no direct evaluation of differences between the plant species, it is notable that the safe site characteristics appeared to be remarkably similar for all five plant species studied. The pattern of establishment depended both on differential seed dispersal and spatial distribution of the seed bank, as well as on species-specific responses in germination and survival (Reader & Buck 1986; Price & Reichman 1987). Seed size and seed morphology have been described as important factors in dispersal and distribution (Rabinowitz & Rapp 1981; Reichman 1984; Peart & Clifford 1987) and are believed to be partly responsible for the floristic diversity and spatial distribution of plants (Sheldon 1974; Chapin 1993). Most of the species we encountered were wind dispersed but not all had small seeds. Our detailed characterizations of safe site requirements involved one large seeded species with wings (A. lasiocarpa), although the remaining four species had small seeds with no such devices. Based on both field and laboratory experiments with four sympatric Erodium species, Stamp (1989) suggested that variation in seed size may mainly account for the ability to take advantage of different seasonal conditions even if species do not colonize different microsites.

Early stages in the life cycle (seed dispersal, seed distribution, germination, etc.) seem more important than subsequent stages in determining the distribution and abundance of plants (Reader & Buck 1986). Hamrick & Lee (1987) concluded similarly that greatest mortality occurs between dispersal and establishment. Distribution of plants in primary successional systems is therefore expected to be determined by the abiotic microenvironment that governs seed trapping, successful germination and establishment. Given the potential importance of drought-induced mortality (Chapin & Bliss 1989), safe sites have received surprisingly little attention in studies of primary succession. In this paper, our intention is to draw attention to the patterns of initial plant colonization as an essential mechanism in defining the plant distribution and spatial community structure in a primary successional habitat. We hope to initiate further interest in the abiotic factors preceding the biotic interactions and mechanisms in primary succession.

Acknowledgements

  1. Top of page
  2. Abstract
  3. Introduction
  4. Materials and methods
  5. Results
  6. Discussion
  7. Acknowledgements
  8. References

This programme was supported by US National Science Foundation Grant DEB-9310006, Emil Aaltonen's Foundation, and the US Forest Service Pacific North-West Research Station. We are grateful for the logistical support of Ken Dull and Al Murphy of the US Forest Service, Wenatchee National Forest, Chelan Ranger District, WA. Ankie Camacho, Lisa Grubisha, Nick Otting, Jamie Platt and Matt Trappe joined the authors for field work and data collection. Ankie Camacho, Leena Ha¨met-Ahti, and Nick Otting aided in plant identification. Lisa Ganio, Manuela Huso and Bruce McCune aided in the experimental design and statistical analyses. The authors are grateful to two anonymous referees, Drs Lindsay Haddon, Dot Helm and Randy Molina for their valuable comments on the manuscript.

References

  1. Top of page
  2. Abstract
  3. Introduction
  4. Materials and methods
  5. Results
  6. Discussion
  7. Acknowledgements
  8. References
  • Ca´zares, E. 1992 Mycorrhizal fungi and their relationship to plant succession in subalpine habitats. PhD Thesis. Oregon State University, Corvallis, OR.
  • Bigwood, D.W. & Inouye, D.W. 1988 Spatial pattern analysis of seed banks: an improved method and optimized sampling. Ecology, 69, 497507.
  • Callaway, R.M. 1995 Positive interactions among plants. Botanical Review, 61, 306349.
  • Chapin, F.S. III 1993 Physiological controls over plant establishment in primary succession. Primary Succession on Land (eds J.Miles & D.W.H.Walton), pp. 161178. Blackwell Scientific Publications, Oxford, UK.
  • Chapin, D.M. & Bliss, L.C. 1989 Seedling growth, physiology, and survivorship in a subalpine, volcanic environment. Ecology, 70, 13251324.
  • Chapin, F.S. III, Walker, L.R., Fastie, C.L. & Sharman, L.C. 1994 Mechanisms of primary succession following deglaciation at Glacier Bay, Alaska. Ecological Monographs, 64, 149175.
  • Connell, J.H. & Slatyer, R.O. 1977 Mechanisms of succession in natural communities and their role in community stability and organization. American Naturalist, 111, 11191144.
  • Crocker, R.L. & Major, J. 1955 Soil development in relation to vegetation and surface age at Glacier Bay, Alaska. Journal of Ecology, 43, 427448.
  • Enright, N.J. & Lamont, B.B. 1989 Seed banks, fire season, safe sites and seedling recruitment in five co-occurring Banksia species. Journal of Ecology, 77, 11111122.
  • Fowler, N.L. 1986 Microsite requirements for germination and establishment of three grass species. American Midland Naturalist, 115, 131145.
  • Fowler, N.L. 1988 What is a safe site? Neighbor, litter, germination date, and patch effects. Ecology, 69, 947961.
  • Franklin, J.F. & Dyrness, C.T. 1973 Natural Vegetation of Oregon and Washington. General Technical Report PNW-8. USDA Forest Service, Washington, DC.
  • Frenot, Y., Gloaguen, J.C., Cannavacciuolo, M. & Bellino, A. 1998 Primary succession on glacier forelands in the subantarctic Kerguelen Islands. Journal of Vegetation Science, 9, 7584.
  • Glenn-Lewin, D.C., Peet, R.K. & Veblen, T.T. 1992 Plant Succession – Theory and Prediction. Chapman & Hall, London, UK.
  • Hamrick, J.L. & Lee, J.M. 1987 Effect of soil surface topography and litter cover on the germination, survival, and growth of musk thistle (Carduus nutans). American Journal of Botany, 74, 451457.
  • Harper, J.L., Clatworthy, J.N., McNaughton, I.H. & Sagar, G.S. 1961 The evolution of closely related species living in the same area. Evolution, 15, 209227.
  • Harper, J.L., Williams, J.T. & Sager, G.R. 1965 The behaviour of seeds in soil. I. The heterogeneity of soil surfaces and its role in determining the establishment of plants from seed. Journal of Ecology, 53, 273386.
  • Hitchcock, C.L. & Cronquist, A. 1973 Flora of the Pacific Northwest. University of Washington Press, Seattle, WA.
  • Holmgren, M., Sceffer, M. & Huston, M.A. 1997 The interplay of facilitation and competition in plant succession. Ecology, 78, 1966–75.
  • Houle, G. 1997 No evidence for interspecific interactions between plants in the first stage of succession on coastal dunes in subarctic Quebec, Canada. Canadian Journal of Botany, 75, 902915.
  • Huenneke, L.F. & Sharitz, R.R. 1990 Substrate heterogeneity and regeneration of a swamp tree, Nyssa aguatica. American Journal of Botany, 77, 413419.
  • Jumpponen, A., Mattson, K., Trappe, J.M. & Ohtonen, R. 1998 Effects of established willows on primary succession on Lyman Glacier Forefront: evidence for simultaneous canopy inhibition and soil facilitation. Arctic and Alpine Research, 30, 3139.
  • Livingston, R.B. 1972 Influence of birds, stones and soil on the establishment of juniper, Juniperus communis, and red cedar. J. virgiana, in New England pastures. Ecology, 53, 11411147.
  • Matlack, G.R. 1989 Secondary dispersal of seed across snow in Betula lenta, a gap-colonizing tree species. Journal of Ecology, 77, 853869.
  • Matthews, J.A. 1992 The Ecology of Recently-Deglaciated Terrain. Cambridge University Press, Cambridge, UK.
  • Matthews, J.A. & Whittaker, R.J. 1987 Vegetation succession on the Storbreen glacier foreland. Arctic and Alpine Research, 19, 385395.
  • McCullagh, P. & Nelder, J.A. 1989 Generalized Linear Models, 2nd edn. Chapman & Hall, New York, NY.
  • Peart, M.H. & Clifford, H.T. 1987 The influence of diaspore morphology and soil-surface properties on the distribution of grasses. Journal of Ecology, 75, 569576.
  • Pickett, S.T.A., Collins, S.L. & Armesto, J.J. 1987 Models, mechanisms and pathways of succession. Botanical Review, 53, 335371.
  • Price, M.V. & Reichman, O.J. 1987 Distribution of seeds in Sonoran dessert soils: implications for heteromyid rodent foraging. Ecology, 68, 17971811.
  • Rabinowitz, D. & Rapp, J.K. 1980 Seed rain in a North American tall grass prairie. Journal of Applied Ecology, 17, 793802.
  • Rabinowitz, D. & Rapp, J.K. 1981 Dispersal abilities of seven sparse and common grasses from Missouri prairie. American Journal of Botany, 68, 616624.
  • Ramsey, F. & Shafer, D. 1996 The Statistical Sleuth: a Course in Methods of Data Analysis. Wadsworth Publishing Company, Belmont, CA.
  • Reader, R.J. & Buck, J. 1986 Topographic variation in the abundance of Hieracium floribundum: relative importance of differential seed dispersal, seedling establishment, plant survival, and reproduction. Journal of Ecology, 74, 815822.
  • Reichman, O.J. 1984 Spatial and temporal variation of seed distributions in Sonoran dessert soils. Journal of Biogeography, 11, 111.
  • Ryvarden, L. 1971 Studies in seed dispersal. I. Trapping of diaspores in the alpine zone at Finse, Norway. Norwegian Journal of Botany, 18, 215226.
  • SAS 1997 SAS/STAT Software: Changes and Enhancements Through Release 6.12. SAS Institute Inc., Cary, NC.
  • Sheldon, J.C. 1974 The behaviour of seeds in soil. III. The influence of seed morphology and the behaviour of seedlings on the establishment of plants from surface-lying seeds. Journal of Ecology, 62, 4766.
  • Stamp, N.E. 1989 Seed dispersal of four sympatric grassland annual species of Erodium. Journal of Ecology, 77, 10051020.
  • Svoboda, J. & Henry, G.R.H. 1987 Succession of marginal arctic environments. Arctic and Alpine Research, 19, 373384.
  • Van Der Valk, A.G. 1992 Establishment, colonization and persistence. Plant Succession Theory and Prediction (eds D.C.Glenn-Lewin, R.K.Peet & T.T.Veblen), pp. 60102. Chapman & Hall, London, UK.
  • Vetaas, O.R. 1997 Relationships between floristic gradients in a primary succession. Journal of Vegetation Science, 8, 665676.
  • Viereck, L.A. 1966 Plant succession and soil development on gravel outwash of the Muldrow Glacier, Alaska. Ecological Monographs, 36, 181199.
  • Watt, A.S. 1919 On the causes of failure of natural regeneration in British oakwoods. Journal of Ecology, 7, 173203.
  • Whittaker, R.J. 1991 The vegetation of the Storbreen gletchenvorfield, Jotunheimen, Norway. IV. Short-term vegetation change. Journal of Biogeography, 18, 4152.
Footnotes
  • Present address: Ecosystems North-West, 6045 NW Happy Valley Dr, Corvallis, OR 97330, USA.

*Present address and correspondence: Ari Jumpponen, Section of Crop Science, Department of Agricultural Research for Northern Sweden, Swedish University of Agricultural Sciences, Box 4097, S-90403 UmeaÅ, Sweden (fax + 46 90 786 94 04; e-mail Ari.Jumpponen@njv.slu.se).