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Fir, Douglas

Fir, Douglas refers to the evergreen coniferous trees of the genus Pseudotsuga, native to western North America.
These tall, majestic trees are known for their distinctive, flat, soft needles and their valuable timber.
Fir, Douglas trees are an important commercial and ecological resource, with applications in construction, furniture-making, and landscaping.
Researchers can explore the scientific literature on Fir, Douglas trees using the powerful PubCompare.ai platform, which provides AI-driven comparisons to help optimize research protocols and unlock new insights into this important tree species.

Most cited protocols related to «Fir, Douglas»

1
Ecology of Southern Yellowstone Ecosystem
Our study area encompassed approximately 2,300 km2 of the Southern Yellowstone Ecosystem (SYE), inclusive of Grand Teton National Park (United States Park Service), the National Elk Refuge (United States Fish and Wildlife Service), and the Bridger-Teton National Forest (United States Forest Service) north of the town of Jackson, Wyoming (Figure 1). Elevations in the study area ranged from 1,800 m in the valleys to > 3,600 m in the mountains. Plant communities included cottonwood (Populus angustifolia) riparian zones interspersed with sagebrush (Artemisia spp.) uplands at lower elevations. At intermediate elevations, aspen (P. tremuloides), Douglas-fir (Pseudotsuga menziesii), and lodgepole pine (Pinus contorta) were the dominant species. Spruce (Picea engelmannii) and fir (Abies lasiocarpa) were the primary tree species at the higher elevations [25 ]. The area was characterized by short, cool summers and long winters with frequent snowstorms. Precipitation occurred mostly as snow, and mean maximum snow depths ranged from 100 cm at lower elevations to > 245 cm at intermediate and higher elevations (2,000 m +).
The study area supported a diverse community of large mammals. Carnivores included wolves, black bears (Ursus americanus), grizzly bears (U. arctos), coyotes (Canis latrans), and red foxes (Vulpes vulpes). Ungulates included elk, mule deer, moose, bison (Bison bison), pronghorn, bighorn sheep, and a very small number of white-tailed deer (Odocoileus virginianus). Deer, elk, bighorn sheep, and pronghorn exhibited seasonal migrations [7 (link),17 ,18 (link),19 (link)].
Elbroch L.M., Lendrum P.E., Newby J., Quigley H, & Craighead D. (2013). Seasonal Foraging Ecology of Non-Migratory Cougars in a System with Migrating Prey. PLoS ONE, 8(12), e83375.
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Publication 2013
Abies Artemisia Bison Black Bears Carnivora Coyotes Deer Ecosystem Fir, Douglas Fishes Forests Grizzly Bears Mammals Mules Odocoileus virginianus Picea Pinus Plants Populus Populus fremontii Sheep, Bighorn Snow Trees Ursus Vulpes vulpes Wolves
2
Rufous Hummingbird Nest Fecal Analysis
Fieldwork was undertaken in coniferous forests (Coastal Douglas-fir Moist Maritime Subzone) on southern Vancouver Island, British Columbia, Canada (48°25′N, 123°28′W; elevation 40–80 m). We collected fecal pellets adhering to Western Red Cedar (Thuja plicata) foliage 1–3 m above ground and adjacent (≤30 cm) to S. rufus nests active during 2017 and 2018 (five from each year). The nests were not disturbed and all samples were collected at least one week after both young had successfully fledged; one nest was sampled the year following active use. Since nest reuse is common in Rufous hummingbirds on Vancouver Island (J Moran, pers. obs., 2017), we were able to obtain samples from two nests that were used in both years. We did not collect samples directly from nests, as spider’s webs are used in nest construction (A Moran, pers. obs., 2017; Healy & Calder, 2006 ), and contamination from web material could potentially result in amplification of DNA from non-prey arachnids. After nesting was completed, the foliage surrounding each nest area was cleared of pellets so no previous years’ samples would be collected in the following year should that nest be reused. We collected pellets directly from the foliage into new Ziploc® bags, which were maintained on ice until transfer to −20 °C for storage (within 5 h). For analysis, single or multiple pellets (≤5) were transferred to 2 ml cryotubes (Fisher Scientific, Waltham, MA, USA) and maintained at −20 °C. Three environmental blanks were obtained from Western Red Cedar foliage >1 m from the ground, at between 5 and 8 m from nests F (Middentop 2018) and J (Middenlow 2018). We applied distilled water to the leaf scales and collected 1.5 ml of wash in a 2 ml cryotube. Following collection, the environmental blank samples were maintained on ice until transfer to −20 °C for storage (within 5 h).
Moran A.J., Prosser S.W, & Moran J.A. (2019). DNA metabarcoding allows non-invasive identification of arthropod prey provisioned to nestling Rufous hummingbirds (Selasphorus rufus). PeerJ, 7, e6596.
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Publication 2019
Arachnida Feces Fir, Douglas Forests Pellets, Drug Plant Leaves Spiders Thuja plicata Tracheophyta
3
Assessing UK Forest Structural Diversity
We collected data from 223 sample points distributed in 24 stands located in eight forests across the UK to consider different species, overstory, and geographical conditions (see Table 1). For each stand, we laid out ten sample points with a random systematic approach. We drew random transects on a desktop map and placed on them evenly spaced points, later identified in the field using a GPS receiver. The distance between points varied with the size of the stand. As most of the stands were originated by artificial planting, transects were not laid out parallel to each other to avoid following the planting lines. When carrying out the field survey, if a sample point fell in an open gap with no overstory, we relocated it under canopy cover if possible; otherwise, it was discarded (thus some stands had <10 sample points).
We assigned to each compartment a categorical variable named OV according to the overstory main species, with the following levels: “broadleaves” for mixed stands composed mainly of European beech (Fagus sylvatica L.) and oaks (Quercus petraea [Matt.] Liebl. and Quercus robur L.); “douglas” for Douglas fir (Pseudotsuga menziesii [Mirb.] Franco), sometimes associated with broadleaves; “larch” for European and Japanese larch (Larix kaempferii [Lamb] Carr. and Larix decidua Mill.); “pine” for Corsican and Scots pine (Pinus nigra subsp. laricio Maire and Pinus sylvestris L.); and “spruce” for Sitka spruce (Picea sitchensis [Bong.] Carr.).
Bianchi S., Cahalan C., Hale S, & Gibbons J.M. (2017). Rapid assessment of forest canopy and light regime using smartphone hemispherical photography. Ecology and Evolution, 7(24), 10556-10566.
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Publication 2017
Beech Decidua Europeans Fagus Fir, Douglas Forests Japanese Larix liposomal amphotericin B Picea Pinus Pinus sylvestris Quercus Substantia Nigra
4
Elk Habitat Dynamics in Redwood Forests
Elk survey data were collected from three distinct sites Davison Meadows and Boyes Meadow, in the Prairie Creek drainage, and the Bald Hills Meadows in the lower Redwood Creek drainage (Fig.2). We primarily selected Boyes Meadow and Bald Hills Meadows because there were no elk population irruptions, as there was in the Davison Meadows, between 1989 and 2011. Another reason for selection was that female elk in Boyes and Davison Meadows displayed strong meadow tenacity (Starns et al. 2014 ). Rarely (observed <1% of time) did the female elk population (defined below) from Boyes Meadow use Davison Meadows, and the Davison females were never observed in the Boyes Meadow (Julian et al. 2013 ). The female population inhabiting the Bald Hills were geographically separated from Boyes and Davison Meadows to the extent that it was unlikely females from these meadows used the Bald Hills or vice versa. Furthermore, the population dynamics of elk in Boyes Meadows and Bald Hills Meadows were very different (see Results). Consequently, to more robustly evaluate the influence of elk herbivory on NDVI during an irruption, temporal patterns in NDVI values in Davison Meadows were compared to NDVI values in Boyes Meadows and the Bald Hills Meadows across the same time period.
All sites are in Redwood National and State Parks in northern Humboldt County, California (Fig.2). The Prairie Creek drainage encompasses about 100 km2 and flows into Redwood Creek. Elevation ranges from near sea level in Davison Meadows to about 1050 m at the highest peak of the Bald Hills. Forest in the Prairie Creek drainage consists mainly of second-growth and old-growth redwood–conifer forests dominated by coast redwood, Sitka spruce (Picea sitchensis), Douglas-fir (Pseudotsuga menziesii), and western hemlock (Tsuga heterophylla). Small meadows (13–51 ha in size) are dispersed throughout the forest. Bald Hills forest consists of a mix of evergreens such as Douglas-fir, with a large component of hardwoods: tanoak (Lithocarpus densiflorus), madrone (Arbutus menziesii), big-leaf maple (Acer macrophyllum), California bay (Umbellularia californica), and red alder (Alnus rubra). Meadows in the Bald Hills are situated near one another and total about 1000 ha. Meadow vegetation at all sites is a mix of perennial and annual grasses such as California oat grass (Danthonia californica), redtop (Agrostis alba) and soft chess (Bromus hordeaceus). Common forbs are hairy cat's ear (Hypochoeris radicata) and narrow-leaved plantain (Plantago lancelata) (Harper 1962 ; Weckerly et al. 2001 ). Since 1997, there has been an apparent increase in reed canary grass (Phalaris arundinacea) in the Davison Meadows.
Regional climate is maritime with mild, dry summers and rainy winters. Coastal fog occurs throughout the year, but is more frequent in summer. Mean minimum and maximum temperatures in the Prairie Creek drainage during winter are approximately 2°C and 10°C, respectively, with mean temperatures in summer ranging from 10 to 20°C (Veirs 1987 ). Annual precipitation is usually greater than 150 cm, with rainfall mostly occurring from autumn to early spring. Snowfall in Boyes and Davison Meadows is rare, and daytime winter temperatures prohibit snow accumulation. The Bald Hills, however, receives snow more frequently and accumulations of 20–40 cm may persist for 1–2 weeks. About 35 km inland, Bald Hills temperatures are more extreme than those found in Boyes and Davison Meadows, with mean summer minimum and maximum temperatures ranging from 20 to 26°C, respectively. Mean minimum and maximum winter temperatures range from 0 to 10°C, respectively.
Starns H.D., Weckerly F.W., Ricca M.A, & Duarte A. (2014). Vegetation changes associated with a population irruption by Roosevelt elk. Ecology and Evolution, 5(1), 109-120.
Publication 2014
Acer Agrostis Alnus Alopecia Bromus Climate Drainage Females Fir, Douglas Forests Hemlock Herbivory Phalaris Picea Plantago Plantago lanceolata Plant Leaves Poaceae Rain Redwood Snow Tracheophyta Tsuga Umbellularia
5
Characterizing Brown Bear Tree Rubbing Behavior
We surveyed principal trails and forest roads (hereafter footpaths) within the study area for RTs from October 2018 to March 2019 (Fig. 1). We looked for trees with rubbing signs such as smoothed bark, discolored surface, scratches, bites, or lack of vegetation at the base; however, the tree was only considered an RT when the presence of bear fur snagged on the bark was confirmed (a characteristic sign of bear tree rubbing behavior). All the trees located within a radius of 5 m around each marked tree (following Clapham et al. 2013 ) were considered control trees (hereafter, CTs). None of the CTs were found to have any evidence of marking. This radius ensured that we sampled trees that showed the same local habitat characteristics as the RT, and that were clearly available to the bear in that location. We followed previous studies on brown bear tree rubbing behavior (Green and Mattson 2003 ; Clapham et al. 2013 ; Sato et al. 2014 ), to characterize each rub and control tree, recording the following variables: (1) tree species (categorical with five levels: birch [Betula spp.], oak [Quercus spp.], chestnut [Castanea sativa], conifer [Pinus spp., Pseudotsuga menziesii], and other); (2) tree status (categorical with two levels: dead and alive); (3) other brown bear tree marks (categorical with three levels: bites, scratches, no other marks); (4) slope exposure, i.e., exposure where the tree was located (categorical with eight levels: north, northeast, east, southeast, south, southwest, west, northwest); (5) tree height, measured with NASA GLOBE Observer v 3.0 (NASA 2019 ); (6) trunk height, i.e., from the ground to the first branch, measured with a tape measure; (7) diameter at breast height (DBH), measured with a diameter tape; (8) distance to the nearest footpath (hereafter dist. to footpath), measured with a tape measure; (9) tree spacing, i.e., average distance to the nearest tree located in each of the four main cardinal directions, measured with a tape; and (10) terrain elevation (m a.s.l.).
González-Bernardo E., Bagnasco C., Bombieri G., Zarzo-Arias A., Ruiz-Villar H., Morales-González A., Lamamy C., Ordiz A., Cañedo D., Díaz J., Chamberlain D.E, & Penteriani V. (2021). Rubbing behavior of European brown bears: factors affecting rub tree selectivity and density. Journal of Mammalogy, 102(2), 468-480.
Publication 2021
Bears Betula Bites Breast Eye Fir, Douglas Forests Pinus Quercus Radius TNFSF10 protein, human Tracheophyta Trees

Most recents protocols related to «Fir, Douglas»

1
Pinaceae Transcriptome Data Collection
From open-access databases, raw transcriptome data for 15 species were downloaded. Among the species, 12 species belong to 10 genera of Pinaceae, including Abies firma, Cathaya argyrophylla, Cedrus deodara, Keteleeria evelyniana, Larix gmelinii, Picea abies, Picea smithiana, Pinus armandii, Pinus elliottii, Pinus massoniana, Pinus taeda, Pseudolarix amabilis, Pseudotsuga menziesii, Tsuga dumosa and Tsuga longibracteata, and the three species Cycas panzhihuaensis, Araucaria cunninghamii, and Platycladus orientalis were used as outgroups (Supplementary Table S1).
Jiang K., Du C., Huang L., Luo J., Liu T, & Huang S. (2023). Phylotranscriptomics and evolution of key genes for terpene biosynthesis in Pinaceae. Frontiers in Plant Science, 14, 1114579.
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Publication 2023
Abies Araucaria Cedrus Cycas Fir, Douglas Larix Picea Pinaceae Pinus Pinus abies Pinus taeda Thuja orientalis Transcriptome Tsuga
2
Predicting Post-Fire Forest Conditions
To predict post-fire stand structure and composition across a range of forests in the interior Pacific Northwest, we integrated datasets from remote sensing, field plots with pre- and post-fire measurements, contemporary forest inventories, and historical forest inventories and reconstructions in a novel modeling approach as shown in Fig 1. To incorporate and assess uncertainty of modeled estimates we used a Monte-Carlo simulation framework that carries estimates of uncertainty through modeling steps. First, we developed species-specific tree mortality models (hereafter “species-level models”) that relate probability of mortality to remotely sensed fire severity (RdNBR) and individual tree size from a field plot network in Oregon and Washington that experienced fire between measurement cycles. Next, we simulated fire by applying species-level models to individual trees within unburned stands in four National Forests in eastern Oregon to predict post-fire stand conditions across the observed range of RdNBR values (hereafter “stand-level models”). We then compared the results of simulated fire in contemporary stands to historical records and reconstructions of forest conditions to determine fire severity ranges that have the highest likelihood to restore historical conditions. Finally, we applied estimates from stand-level models to an example burned landscape to demonstrate the use of these methods for post-fire assessment and management (hereafter “landscape-scale model”).
We developed tree mortality models using a regional dataset and applied them to assess restorative fire severity ranges in eastern Oregon. The regional dataset primarily included plots from dry forest systems, but also included plots burned within fires in the Oregon Klamath Mountains, Oregon Cascades, and Washington North Cascades (Fig 1 in S1 Appendix). The eastern Oregon focal area is characterized by warm summers, cold winters, and precipitation falling mostly as snow [21 (link)]. Historically, fire-tolerant ponderosa pine was the dominant overstory species at lower elevations and co-occurred with western larch (Larix occidentalis) in northeastern Oregon. Less fire-tolerant white fir (Abies concolor), grand fir (Abies grandis), and Douglas-fir (Pseudotsuga menziesii) occurred as components of mixed stands at higher elevations and in more mesic topographic settings [67 (link)]. Before Euro-American colonization, frequent, low severity fire (8–31-year return intervals) maintained forests conditions that were relatively resistant to fire, drought, and native pathogens [21 (link), 68 (link)]. Fire exclusion due to decreased cultural burning, land use changes, and fire suppression policies has increased the abundance of less fire-tolerant species and overall forest density across these landscapes [21 (link), 65 (link)].
Greenler S.M., Dunn C.J., Johnston J.D., Reilly M.J., Merschel A.G., Hagmann R.K, & Bailey J.D. (2023). Too hot, too cold, or just right: Can wildfire restore dry forests of the interior Pacific Northwest?. PLOS ONE, 18(2), e0281927.
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Publication 2023
Abies Cold Temperature Droughts Fir, Douglas Forests Larix pathogenesis Personality Inventories Pinus ponderosa Reconstructive Surgical Procedures Snow Trees
3
Red Squirrel Translocation in Arizona
We translocated squirrels using two study sites in the Apache-Sitgreaves National Forest in the White Mountains (Arizona, USA). The first study site was near Big Lake (UTM coordinate: 12S 647118.39216871 3750447.4959222), while the second site was near Hannagan Meadow (UTM coordinates: 12S 655714.23295814 3723357.028484). Both sites had similar elevation, between 2650–2750 m and mixed conifer forest type. Common species were Douglas fir (Pseudostuga menziesii), blue spruce (Picea pungens), corkbark fir (Abies lasiocarpa), Engelmann spruce (Picea engelmannii), ponderosa pine (Pinus ponderosa), southwestern white pine (P. strobiformis), and aspen (Populus tremuloides) [25 ]. The sites are 32 km apart.
We used Big Lake in fall and Hannagan Meadow in winter due to road accessibility (the road to Big Lake is close in winter). Although it is possible season might be confounded with location, both sites have stable red squirrel populations and the same vegetation type and structure suggesting this is unlikely.
All animals were translocated to areas inhabited by other red squirrels due to difficulty of finding areas that had no established squirrels yet met the environmental requirements for settlement. Releasing animals into an occupied area, can have different outcome than releasing animals in an empty environment. However, the recovery plan for this species includes the augmentation of the population (from captive-breed individuals) following the first year of release in the unoccupied habitat. In this situation, the response of the translocated individuals from this study will provide important information on translocation strategies.
Morandini M, & Koprowski J.L. (2023). Using a substitute species to inform translocation of an endangered territorial mammal. PLOS ONE, 18(2), e0271083.
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Publication 2023
Abies Animals Fir, Douglas Forests Picea Pinus Pinus ponderosa Populus Squirrels Tracheophyta Translocation, Chromosomal
4
Comparative Forestry Study in Germany
The study was conducted in the federal state of Lower Saxony in northwest Germany. The 40 study plots were located in eight study sites, with each site comprising five different forest stands (plot “quintets”; [69 ]). These stands were pure stands of native European Beech (F. sylvatica), native Norway Spruce (P. abies), and non-native Douglas fir (P. menziesii), and mixed stands of beech-Douglas fir and beech-spruce. Within sites, distances between plots ranged from 76 to 4600 m. Each of the 40 plots had a size of 0.25 ha. The eight sites were divided into four northern sites and four southern sites [69 ]. Between site distances ranged from 5 to 190 km, with 105 km as the minimum distance between northern and southern sites. This division of sites allows testing for effects of different environmental conditions of forest stands, as site characteristics vary between the two regions. In the northern, sandy sites, precipitation is lower (708 mm mean annual precipitation) and the soil is nutrient-poor due to dry dystrophic sand deposits [70 ]. The southern, loamy sites have higher precipitation (888 mm mean annual precipitation) and are richer in nutrients due to their spodic cystric cambisols soil characteristics [70 ]. Tree ages were 80 years on average, ranging from 43 to 131 years [32 ].
Benjamin W., Riko F., Dragan M., Jing-Zhong L., Peter K., Stefan S, & Andreas S. (2023). Conifers and non-native tree species shift trophic niches of generalist arthropod predators in Central European beech forests. BMC Ecology and Evolution, 23, 3.
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Publication 2023
Abies Beech Europeans Fir, Douglas Forests Nutrients Picea Trees
5
Trophic Niche and Forest Characteristics
We used several structural parameters to relate trophic niche metrics to stand characteristics on plot level: relative area potentially available (APA) of Douglas fir and Norway spruce as a measure of tree proportions, neighborhood diversity (NDiv), canopy openness, herb vegetation complexity and deadwood volume. We included relative tree proportions to account for different mixture proportions in our plots. For the calculation of APA, plots were divided into pixels, which then were assigned to the closest trees, whilst the trees are weighted with their size [75 ]. NDiv accounts for possible effects of tree diversity. NDiv is a novel index of spatially explicit diversity, using the number of monospecific and heterospecific neighbors bordering the APA of each tree. This individual tree-based calculation avoids high scores for plots with monospecific patches of different tree species [76 ]. NDiv values range between 0 (monospecific) and 1 (heterospecific). Canopy openness, herb vegetation complexity and deadwood volume are important community-shaping parameters for forest floor-associated arthropods [19 , 60 , 63 ]. We measured canopy openness at the center of each trap using a Solariscope (SOL 300, Ing.-Büro Behling, Hermannsburg). For herb vegetation structure we divided each 10 × 10 grid cell around the traps into 4 quartiles and measured each quartile. We assessed herb vegetation complexity by counting all points where plant material touched or intercepted strings of 30 cm length at the heights of 3, 10, 20, 30, 40 and 50 cm. For total deadwood volume (m3/ha), we measured all stumps and logs with a diameter > 5 cm across the entire sampling grid. All structural parameters were averaged on the plot level.
Benjamin W., Riko F., Dragan M., Jing-Zhong L., Peter K., Stefan S, & Andreas S. (2023). Conifers and non-native tree species shift trophic niches of generalist arthropod predators in Central European beech forests. BMC Ecology and Evolution, 23, 3.
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Publication 2023
Amputation Stumps Arthropods Fir, Douglas Forests Grid Cells Picea Plants Trees

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