Fire Effects Information System (FEIS)
FEIS Home Page

Paulownia tomentosa


  Princesstree in postfire habitat in Linville Gorge Wilderness Area, North Carolina. Photo by Dane Kuppinger.
Innes, Robin J. 2009. Paulownia tomentosa. In: Fire Effects Information System, [Online]. U.S. Department of Agriculture, Forest Service, Rocky Mountain Research Station, Fire Sciences Laboratory (Producer). Available: [].



princess tree
royal paulownia
empress tree
kiri tree

The scientific name of princesstree is Paulownia tomentosa (Thunb.) Sieb. & Zucc. ex Steud. [45,73]. A review [3] stated that botanists have historically debated the taxonomic classification of princesstree, placing it within either the figwort (Scrophulariaceae) or trumpet-creeper (Bignoniaceae) family. Based on floral anatomy, embryo morphology, and seed morphology, princesstree is placed in Scrophulariaceae, a family of mostly herbaceous species [3,62,158]. Princesstree is a popular ornamental, and several cultivars have been developed [62,115,123].

Paulownia imperialis Sieb. & Zucc. [62]



Information on state-level noxious weed status of plants in the United States is available at Plants Database.


SPECIES: Paulownia tomentosa
Princesstree is nonnative in North America. It occurs from Montreal, Canada, south to Florida and west to Texas and Indiana; it has also been planted in coastal Washington [101] and California [62]. Princesstree has escaped from cultivation and spread extensively to portions of the southeastern and middle Atlantic states [63,95,126]. It is invasive from Pennsylvania south to Georgia and west to Missouri (see Impacts) [10,71]. The Plants Database provides a distributional map of princesstree in the United States.

Princesstree is native to eastern and central China [63,158], where it occurs south of the 32 °F (0 °C) isotherm (see Climate) [63]. With the exception of Antarctica, princesstree has been cultivated in every continent of the world [30,34,37,57,61,62,63,78,133,149]. It was most frequently introduced as a crop tree but also as an ornamental. Princesstree appears to be less invasive in Europe than in North America [43,115,133]. However, it has received research attention in Europe due to increases in the number of localities where it has been observed since the 1980s [43]. In Australia, princesstree is considered potentially invasive [30,62]; invasiveness in other foreign countries had not been reported as of this writing (2009).

Plant community associations of nonnative species are often difficult to describe accurately because detailed survey information is lacking, there are gaps in understandings of nonnative species' ecological characteristics, and nonnative species may still be expanding their North American range. Therefore, princesstree may occur in plant communities other than those discussed here and listed in the Fire Regime Table.

Princesstree occurs in a variety of habitats and plant associations throughout the eastern United States that are similar to those of its native range (see Site Characteristics). It may be a minor, occasional, or important component of plant communities of which it is a part. For example, in debris avalanches following Hurricane Camille in central Virginia, princesstree established at densities ranging from 75 to 310 stems/ha on 3 of 4 study sites dominated by yellow-poplar (Liriodendron tulipifera), sweet birch (Betula lenta), black locust (Robinia pseudoacacia), and red maple (Acer rubrum); in this study, its importance value ranked 12th among 15 tree species recorded [64]. In a streamside forest in central Virginia, it had the lowest importance value among the 4 dominant forest trees of the study area (yellow-poplar, sweet birch, and sycamore (Platanus occidentalis)) [146]. In northern Delaware, princesstree was present in 1 of 12 study sites; the site was a relatively undisturbed hardwood forest dominated by yellow-poplar, American beech (Fagus grandifolia), black oak, (Quercus velutina), white oak (Q. alba), and red oak (Q. rubra) [122]. In intact forest of Loess Bluff Ravines in western Kentucky, Bryant [22] reported low importance of princesstree in sugar maple (Acer saccharum)-American beech-sweetgum (Liquidambar styraciflua) forest; in this study, princesstree ranked 21st in relative importance among 27 tree species. Although Bryant [22] considered princesstree a minor component of plant communities across all 4 counties covered by Loess Bluff Ravines, Wilson [150] categorized it as a possible indicator species of the Backcut Loess habitat in Sandy Branch, a part of Loess Bluff Ravines in Carlisle County, Kentucky.

In other parts of the eastern United States, princesstree occurs in disturbed upland areas associated with early-successional species such as maple (Acer spp.), oak (Quercus spp.), and pine (Pinus spp.). Common associates on disturbed sites in Blue River Gorge in the Blue Ridge Mountains of Virginia include Virginia pine (P. virginiana), red maple, American elm (Ulmus americana), blackjack oak (Q. marilandica), eastern redbud (Cercis canadensis), sassafras (Sassafras albidum), sweet birch, and smooth sumac (Rhus glabra) [109]. Princesstree was described as an "aggressive" invasive species within disturbed areas at the Oak Ridge National Environmental Research Park in Tennessee; at this site, adjacent uplands were characterized by 2nd- and 3rd-growth oak-hickory-maple forests [44]. In the Great Smoky Mountains National Park, Tennessee, princesstree occurred by streams with yellow-poplar, sweet birch, and sycamore [8]. In eastern Pennsylvania, princesstree was a minor component in a 5-acre (2 ha) mixed-hardwood forest gap. Allegheny blackberry (Rubus allegheniensis) and American pokeweed (Phytolacca americana) dominated the vegetation of the tornado-formed gap [66]. Along the Green River Gorge, North Carolina, princesstree was locally abundant within disturbed cove hardwood forest dominated primarily by yellow-poplar and basswood (Tilia americana) [107]. Along a 250-mile (402 km) reach of the New River Gorge in West Virginia, princesstree was found at 5 of 34 sites; these sites included a yellow-poplar-white oak-red oak-sugar maple forest, midelevation quartzite rocky summits and cliff faces, a black willow-river birch (Salix nigra-Betula nigra) streambed, and disturbed areas [128]. In Bent Creek Experimental Forest in Asheville, North Carolina, it was a minor component in 4-year-old postclearcut forest dominated by yellow-poplar, sweet birch, black locust, and sassafras [89]. In the Appalachian Mountains from central Pennsylvania to northern Georgia, princesstree occurred in fire-adapted Table Mountain pine-pitch pine (Pinus pungens-P. rigida) forests, which commonly occur on xeric ridgetops and southwest-facing slopes at midelevations [40,148]. Princesstree occurs frequently on burned ridges with pitch pine and bigtooth aspen (Populus grandidentata) on Bull Run Mountain in northern Virginia [2]. In Great Falls Park in Fairfax County, Virginia, it occurred in American beech-white oak-red oak-yellow-poplar forest with American holly (Ilex opaca) and Christmas fern (Polystichum acrostichoides) in the understory [124]. At Inwood Hill Park in New York County, New York, princesstrees >4 inches (10 cm) DBH were found in valley forest and ridgetop communities at densities ranging from 0 to 13 stems/ha [46]:

Density per ha of subcanopy (10-30 cm DBH) and canopy (>30 cm DBH) princesstree found in 2 forest types in Inwood Hill Park, New York [46]
DBH (cm)
Forest type 10-30 >30
Valley 0 9
Ridgetop 13 13

Sugar maple, yellow-poplar, red oak, chestnut oak, black locust, and black cherry (Prunus serotina) dominated the canopy and subcanopy of the valley forest community in this area. Yellow-poplar, white oak, and red oak dominated the canopy of the ridgetop community, while mulberry (Morus spp.), black cherry, plumleaf crab apple (Pyrus prunifolia), and red maple dominated the subcanopy [88]. For more information regarding the ecological range of princesstree, see Site Characteristics and Successional Status.


SPECIES: Paulownia tomentosa
  Botanical description: The following description of princesstree provides characteristics that may be relevant to fire ecology and is not meant for identification. Keys for identification are available (e.g., [45,63,104,108,158]).

Princesstree is a deciduous tree [10,62] that may reach 69 to 105 feet (21-32 m) in height and 3.9 to 6.6 feet (1.2-2.0 m) DBH at maturity, although it is typically smaller [10,41,49,126]. At maturity, it has thin, flaky bark [126]. Princesstree tends to be branchy or multistemmed when grown in the open but can have a straight bole in forests [78,130,133]. Branches are stout but brittle, because the pith is chambered or hollow and markedly flattened at the nodes [10,41,126]. Leaves of adult trees are typically 6 to 12 inches (15-30 cm) long and 4 to 8 inches (10-20 cm) wide. However, leaves of juvenile plants and those of stump sprouts may be much larger; for example, juvenile leaves have been observed as long as 3 feet (0.9 m) [51,138], and leaves of stump sprouts may reach 20 to 30 inches (50-80 cm) or more in length (see Vegetative regeneration) [10,41,108,126]. Brittle branches and large leaves make princesstree prone to wind damage and as a result, twigs, seed capsules, and other debris frequently accumulate under the tree canopy [15,62,115,130]. The inflorescence is a large, erect terminal panicle 6 to 12 inches (15-30 cm) long with 2- to 2.5-inch (5-6 cm) long, tubular flowers. The fruit is an oval, 2-part capsule, 1 to 2 inches (2.5- 4 cm) long and 1 inch (2.5 cm) in diameter [10,41,62,126]. Each part of the capsule has 2 compartments that contain very small (1.5-3 mm long), winged seeds [10,17,108]. The capsules and large, fully-developed flower buds are conspicuous in winter [126]. Roots can be relatively shallow to deep and well developed, apparently depending upon soil conditions. They are typically widely spreading without a strong taproot [4,10,29,62,63,79,130,158].

Princesstree in flower. Photo courtesy of Leslie J. Mehrhoff, University of Connecticut,

A clumped stand structure can result from even-aged seedling establishment after disturbance or from expansion through root sprouting [41,96]. Establishment of princesstree in streamside forest in Virginia associated with the large-scale disturbance of Hurricane Camille resulted in even-aged princesstree stands 10 years after the hurricane [146]. Forty-three percent of recorded princesstree populations in Austria resided within monospecific stands; this was attributed to the species' ability to invade extremely dry sites after disturbance [43].

Life span: Princesstree is apparently short lived. According to a review, mature princesstrees are often structurally unsound and rarely live more than 70 years [10]. However, another review reports that its life span is over 125 years [78].

Raunkiaer [110] life form:

According to reviews, princesstree pollen is fully developed before winter [62], and pollination occurs in spring [10,102]. Flowers bloom before the leaves begin to emerge in late April or early May [41,65,123]. Leaf expansion begins about 2 weeks after flowering. Flower buds begin to appear in the leaf axils in late July or early August [24,51,63]. They develop through summer, mature in October, and are visible as terminal panicles after leaves fall in autumn [24,51]. Leaves are retained in autumn until after the first frost [123]. Seeds mature in September, and capsules ripen and open in October [27]. The capsules may remain on the tree for long periods [65]. The capsules break open and seeds are disseminated by wind throughout winter and into spring [16].


Princesstree reproduces from seed and by sprouting from adventitious buds on stems and roots [37,63]. It apparently sprouts with or without top-kill [101]. Both methods of reproduction are important to its reproductive success and invasiveness.

Pollination and breeding system: Flowers are pollinated by a variety of nectar- and pollen-feeding insects [10,102].

Seed production: Princesstree produces many small, light seeds. Seeds weigh about 0.17 mg each [16,31,138]. A single seed capsule may contain as many as 2,000 seeds [10,62], so an individual tree may produce 20 million or more seeds/year [130]. In a review, Bonner [17] provides the following information on princesstree fruit and seed collected in southeast Arkansas:

Measures of princesstree fruits and seeds in Arkansas [17]
Fruits/L 88
Seeds/fruit 2,033
Seeds (g)/fruit (L) 28
Seeds/g 6,200
Moisture content (% fresh weight) 7

Princesstree reaches reproductive age early. Time to maturity depends upon environmental conditions. It may flower in favorable environments in its 4th or 5th year [78,79,101]; under cultivation it may flower as early as the 3rd year [130]. Hu [63] reports that Paulownia first flowers at 8 to 10 years of age under "suitable" conditions in China.

Seed dispersal: The small, light, winged seeds of princesstree are easily transported by wind and water over considerable distances [10,41]. Field observations suggest that seedlings are occasionally located more than 2 miles (3 km) from parent trees in mountainous regions of North Carolina and Tennessee [79,84]. This evidence led Kuppinger [79] to suggest that "only the largest blocks of uninvaded forest may have areas where invasion of princesstree is precluded by distance-induced dispersal limitations".

Seed banking: Although there is disagreement regarding the persistence of princesstree seeds within the seed bank, it appears that princesstree develops a transient seed bank. Seeds can survive in the soil seed bank for at least 2 to 3 years [67,79,90]. They may persist longer [36,90], but long-term field studies on princesstree seed longevity were lacking as of 2009 [17].

Some studies found evidence for a persistent princesstree seed bank. The species composition and density of seeds within the seed bank of 2nd-growth deciduous forest soils were examined in eastern Tennessee. Seeds were collected at 3 depths (litter layer, 0-2 inches (0-5 cm), and 2-4 inches (5-10 cm)) and germinated in a greenhouse. Viable princesstree seeds were found at each depth, but a majority (82%) of the germinants emerged from the 0- to 2-inch and 2- to 4-inch soil depths. The author concluded that the presence of viable seeds at depths as great as 4 inches (10 cm) was a strong indication that princesstree seeds may accumulate and remain dormant in the seed bank for long periods of time, and that this species "might be expected to appear should the canopy open up and early successional conditions prevail" [36]. In field experiments in Ohio, mortality of princesstree seeds was relatively low (21% (SE 3.3)) after 3 years. Seed dormancy was variable and significantly affected by harvest date, soil profile position, and location (P<0.001 for all variables). The author concluded that princesstree formed a persistent seed bank and estimated that seeds could survive in the soil for up to 15 years [90].

In contrast, no evidence of a persistent princesstree seed bank was found in soils of American beech-northern red oak-white oak-black oak-scarlet oak (Q. coccinea) forest in southeastern Pennsylvania. In this study, low seed survival rates (<30%) and low germination (1.7%) under field conditions over the course of 2 years suggested that princesstree did not form a persistent seed bank. These authors characterized princesstree's seed bank as large, with very high turnover and little between-year build-up, and suggested that seed banking was probably not important to princesstree regeneration [67]. High density of princesstree seeds within the seed bank may not indicate high rates of germination and establishment after disturbance. Hyatt [66] observed that princesstree seeds "rarely, if ever, germinate" in wildlands and "when they do germinate, they rarely survive more than a year" (see Seedling establishment).

Long-distance dispersal and prolific seed production of princesstree apparently allow it to establish a transient seed bank from on- and off-site sources. In 2nd-growth deciduous forest soils of Tennessee, viable princesstree seed was found in the seed bank, though no mature princesstrees were present in the overstory [36]. Similarly, though no mature princesstrees were present within the vegetative overstory, seed was observed in the seed bank of the pine (pitch pine and shortleaf pine (Pinus echinata)) barrens region of southern New Jersey and a Delaware River tidal freshwater marsh in northern New Jersey [86,92]. In debris avalanches following Hurricane Camille, princesstree established at densities up to 310 stems/ha, despite its absence from adjacent, undisturbed hardwood forest [64]. Similarly, it was very abundant (18%) in the seed bank in southeastern Pennsylvania at a site dominated by oak (red oak, white oak, and black oak) and American beech; however, only 2 mature princesstrees were present [66].

Germination: Princesstree seed longevity appears to be relatively short (see Seed banking). Seed germination capacity decreases from the time of dispersal even under optimal storage conditions in the laboratory [27,34,51,52]. One study found that cold-stratified seeds frequently maintained high germination rates (>90%) in the laboratory even after 3 years [17]. Other studies report that germination of cold-stored seeds appeared to decline sharply after 4 years, with highest germination occurring <2 years from the time of dispersal [26,51,52].

Unlike seeds of many native trees that commonly occur with princesstree (e.g., oak, beech (Fagus spp.), and aspen (Populus spp.)), princesstree seeds can maintain high viability despite dehydration [9]. The seeds require light for germination [18,157]. The light requirement for germination was considered "unusually high" when compared with other species [31]. The actual period of illumination required ranges from minutes to hours and varies with seed source, year, and storage conditions [18,55].

Princesstree seeds are not dormant when dispersed from the mother plant [17,79,155]. In Arkansas, 90% of seeds germinated within 19 days of collection [17]. Thus, fresh, wind-blown seeds dispersed in late summer and early fall may germinate immediately if they reach suitable habitat [63]. Secondary dormancy can be induced by unfavorable environmental conditions after dispersal. Seeds can be readily induced into secondary dormancy in the laboratory by moist or dry stratification at cold temperatures (approximately 40 °F (4 °C)) or imbibing seeds in darkness [55,157].

The effect of secondary dormancy on germination is highly variable and partially depends upon the amount of time in darkness and the duration of the low temperature exposure [54,79]. Secondary dormancy may alter the time to germination and the rate of germination in this species, and in some cases, it may reduce or eliminate the light requirement of the seed and expand the range of temperatures in which germination occurs [7,17,27,28,51,52,54,157]. Seeds overwintered in the seed bank may achieve high germination rates in the spring [7,27] despite low light or temperature. Seeds may acquire secondary dormancy but fail to germinate if the conditions for breaking the dormancy are not met. In the laboratory, numerous mechanisms break secondary dormancy in princesstree (see [90] and [54] for more information). Smoke was an important chemical stimulus for the germination of seeds in the laboratory (see Fire Management Considerations) [132].

According to reviews, princesstree prefers high light, exposed mineral soil, and adequate moisture for germination and establishment [18,26,63,130]; however, results of experimental studies are variable and often difficult to reconcile given the effect of environmental conditions on germination capacity and dormancy. In field experiments in Ohio, germination of naturally cold-stratified seeds was measured on different substrates and across light (intact forest, edge, and 7-year-old clearcut) and substrate (bare mineral soil, sand, gravel, cobble, top soil, and leaf litter) gradients. Germination was low overall (15%) and occurred only under full light (clearcut). During the 1st year of the study, a drought year, germination was observed only in cobble and gravel. In the 2nd year, with average precipitation, germination was significantly greater on bare mineral soil than any other substrate (P=0.05). The difference in germination between the 2 years was attributed to presence of moist microclimates in the cobble and gravel during the drought. Seeds buried 2 inches (5 cm) in the soil had greater tendency to become dormant and had lower mortality than seeds stored at the soil surface [90]. In contrast, a greenhouse study subjected seeds that had been dry-stored at ambient temperatures to 2 light treatment levels (full sun and 50% shade), 2 surface-cover treatment levels (bare soil and 1-inch (2 cm) litter cover), and 3 seed position treatments (litter surface, soil surface, and 1 inch beneath the soil surface). Germination rates under 50% shade were significantly higher than germination rates under full sun, with the highest germination levels recorded under 50% shade in bare soil on the soil surface (P<0.001 for all variables). In addition, germination was significantly lower when litter was present than when litter was absent regardless of light level, and buried seeds had significantly lower germination rates than those on the soil surface (P<0.001 for all variables) [79]. Despite their contrasts, these studies agree that leaf litter inhibits germination of seeds and that buried seeds will likely remain dormant until disturbance brings them up to the soil surface. See Site Characteristics for additional information on the effects of soil moisture, pH, fertility, and texture on seed germination.

Seedling establishment: Princesstree seedling establishment may be infrequent and widely scattered [26,62,66,129,152]. For example, on Staten Island, New York, seedlings volunteered on a restored landfill site planted with native woody species. A year after restoration plantings, princesstree count on fifty 10 × 30 meter plots totaled 1 seedling, among the lowest of 32 volunteer taxa [113]. Many studies have detailed the difficulties of establishing princesstree in plantations in the United States under intense silvicultural practices and controlled environmental conditions (e.g., [13,127]). Even so, princesstree has successfully expanded its range through seeding establishment [113] and may be more common than indicated in the literature. For example, princesstree was characterized as the 2nd and 5th most successful nonnative tree invading native communities in the Northeast [102] and Southeast [97] as of 1986 and 2008, respectively (see Impacts).

Plant growth: Once established, princesstree growth may be rapid [41,58], and survival may be high [129] even in harsh environments, but reports are variable. Aboveground growth of seedlings is typically slow during the first year [34,62], when seedlings invest heavily in belowground growth [90,91]. Johnson and others [70] report a 220% increase in root growth of young seedlings over a 3-year period in field experiments in Virginia. Rapid seedling root development makes this species difficult to control (see Control). A shift in emphasis from belowground to aboveground biomass accumulation occurs between the 1st and 2nd year [90]. In reviews, height increases of over 7 feet (2 m)/year have been reported for cultivated Paulownia seedlings [37]. Many authors report findings on perhaps extraordinary individuals. A 20-year-old princesstree observed in Kentucky had a diameter of 14 inches (36 cm) and reached a height of 62 feet (19 m) [144]. Typically, however, growth rate is much less. For example, mean annual height growth of seedlings after direct seeding on surface-mine spoils in eastern Kentucky averaged 24 inches (60 cm)/year [129]:

Establishment and growth of princesstree 1 and 5 years after direct seeding on surface-mine spoils in eastern Kentucky [129]
Stocking* after 1st growing season (%) Stocking* after 5 years (%) Survival after 5 years (%) Mean height after 1 year (cm) Mean height after 5 years (cm) Mean annual growth/year (cm)
1 <1 80 11.3 250.5 60
*Stocking defined as the percent of direct-seeded plots (n=1,080) with princesstree seedlings.

Johnson and others [70] report high survival of seedlings on control plots 1 year after planting (99.5% in 1994) but decreased survival in subsequent years (range: 44.8% in 1995 to 10.7% in 2000). Low survival of seedlings in this and other studies has been attributed to late spring frosts, drought, disease, damaging wind, herbivory, and interference from neighboring vegetation [15,70,90,98,105].

Light availability can impact seedling establishment, survival, and growth. Photoperiod is an important factor influencing seedling height growth, with rate and duration of height growth increasing with lengthening photoperiod in the laboratory (e.g., [24,68,116]). Photoperiod also influences root development. Root length of princesstree seedlings increased nearly 2-fold when the photoperiod was increased from 8 to 12 hours in the laboratory (P=0.05); increasing photoperiod beyond 12 hours further increased mean root length, but not significantly [24]. When the effects of herbivory were removed, princesstree seedlings planted in 7-year-old clearcut oak (white, red, and black oak)-hickory (pignut (Carya glabra) and shagbark hickory (C. ovata)) forest had greater percent survivorship (70.5% (SE 5.9)) than seedlings in either edges (47.5% (SE 3.6)) or intact forests (48.5% (SE 6.3), P<0.05), perhaps due to greater light availability in clearcuts. Plants in low light (intact forest) had slower growth rates, thinner leaves, and higher specific leaf area and leaf area ratios than those in edges and clearcuts [90]. See Site Characteristics for additional information on the effects of soil moisture, pH, fertility, and texture on seedling establishment and plant growth.

Vegetative regeneration: Vegetative regeneration is important to princesstree's persistence and spread because sprouting may allow an individual to persist after defoliation or disturbance. Princesstree sprouts from adventitious buds on stems and roots, apparently with or without top-kill [4,10,29,37,62,63,79,115,130,158]. Sprouts generally grow faster than seedlings. For example, root sprouts may grow to over 15 feet (5 m) in a single season [10]. Thus, coppicing is a common strategy employed by nurseries and plantation farmers to stimulate rapid growth of seedlings (e.g., [130]), which are typically slow growing initially (see Plant growth). In a common garden experiment, seedlings subjected to cutting sprouted at 4 weeks after germination even in low light, although older seedlings and those grown in full sun were more likely to survive and produce new shoots. Cut plants had greater mortality than uncut plants overall [91].

Little information is available on princesstree's natural habitat in China, largely because princesstree has a long history of cultivation there, and much of its native range has been altered by human activities [62]. In China, princesstree is a minor component of the deciduous mesophytic forest, growing chiefly in mesic ravines, open valleys, and disturbed areas associated with species of maple, ash (Fraxinus spp.), oak, chestnut (Castanea spp.), basswood (Tilia spp.), and pine [62,63]. The following distribution information of princesstree in China is provided by Zhu and others [158]:

Distribution of princesstree in its native range in China [158]
Latitude 28-40 °N
Longitude 105-128 °E
Altitude (m) 1,500
Temperature (°C)
Maximum 40
Minimum -20
Annual (mm) 500-1,500
Dry months September to March
pH 5-8.5
Texture light clay to sand

In the eastern United States, princesstree occurs in a variety of disturbed, high-light environments including forest gaps and edges, streambanks and scoured riparian areas, steep rocky slopes—particularly south slopes where solar radiation is high—roadsides, fencerows, vacant lots, and "waste" places [10,11,31,41,49,51,58,71,85,93,108,112,126,130,138,146,147,153]. Seed germination and seedling establishment are optimum in disturbed areas with exposed mineral soil, high light, and little to no litter (see Germination) [18,63,130]; thus, princesstree frequently establishes and spreads after disturbances that create these conditions, such as fire, windstorms, pestilence, floods, landslides, and anthropogenic disturbances such as construction, cultivation, mining, and logging [10,44,51,64,84,90,97,113,118,131,146]. See Impacts for more information.

Soils: According to reviews, princesstree tolerates a variety of soil types and conditions including low fertility, high acidity, and drought [10,37,112,130] but grows best on moist, uncompacted, well-drained soils [14,17,37,51,52,127,133,138]. In Virginia, field observations suggest that drought may have reduced princesstree seedling survival and growth [70]. In field experiments in Ohio, overall survivorship of experimentally planted seedlings across 3 habitats (intact forest, edge, and clearcut) was reduced in a drought year (P<0.0001) [90].

Best growth of princesstree is obtained within strongly acidic to mildly alkaline pH levels (range: 5.5-7.5) [14,52,95,127,130,133,136,143,158]. High soil acidity adversely affects germination and seedling growth [136]. Germination, as well as seedling root and shoot growth, are typically poor at soil pH of <4.0, but seedling growth may be reduced at soil pH of <5.0 [95,136]. Seeds are likely killed at soil pH of <2.5. A gradual increase in seed germination was observed in the laboratory from pH 4 to pH 7, with 79% and 98% germination at pH 4.0 and 7.0, respectively. Time required for maximum seed germination was negatively correlated with acidity (r²=0.96, P<0.05). Princesstrees in treatments with soil pH of <5.0 germinated more quickly and primary root growth occurred more slowly than princesstrees in treatments with soil pH of >6.0 [136]

Soil texture may play a role in princesstree's invasiveness. In general, sandy or loamy soils with low clay content appear optimum [14,52,127,158]. In China, princesstree generally grows on soils where clay content is <10% [158]. In the United States, production guides recommend planting princesstree on soils with <30% clay content [52,74]. In urban wetlands of northeastern New Jersey, princesstree abundance increased as soil sand content increased (odds ratio=0.91, P=0.001) and clay content decreased (odds ratio=1.07, P=0.01) [42]. Princesstree growers in the southeastern Piedmont region of Virginia reported decreased growth and survival on heavy clay soils; however, intense soil disturbance (i.e., soil trenching) ameliorated the effects of heavy clays [70].

In general, survival of seedlings appears highest in disturbed soils. For example, in field experiments in Illinois, survival of seedlings was significantly higher (P=0.01) on sites that had been plowed and disked (68%) than on zero-till sites (40%); these results were attributed to improved aeration of the uncompacted soils and to reduced cover of fescue (Vulpia spp.) and other annual grasses that resulted from the disturbance [5].

Nitrogen and phosphorus are essential for tree growth. Since fire may result in substantial short- and long-term changes in availability of these nutrients (see [76] for a review), knowledge of princesstree's nitrogen and phosphorus requirements may yield important information regarding its postfire establishment and spread. In general, princesstree is tolerant of low soil fertility but grows better in fertile soils, responding favorably to fertilizer by increasing growth [15,37,127]. Melhuish and others [95] report that nitrogen and phosphorus levels providing the best growth for princesstree seedlings in a field experiment (100 N:5 P) were about half those required by native red maple, indicating that princesstree may be more competitive than red maple in soils low in nitrogen and phosphorus. However, the authors note that the study was limited in scope and that further tests—including higher phosphorus levels—should be conducted [95]. Results of Jia and Ingestad [69] suggest that higher levels of phosphorus than those reported by Mehuish and others [95] are optimal for princesstree. These authors conducted an experiment to determine the optimum nutrient proportions for princesstree and found that high relative growth rate was obtained at 100 N:75 K:20 P:8 Ca:9 Mg [69]. High nitrogen levels may allow princesstree to increase chlorophyll content of leaves and maintain growth in low light [90]. Paulownia is endomycorrhizal [37,106], but according to Donald [37] the genus is not strongly dependent upon symbiotic fungi for resource uptake.

Climate: Cold climates may limit princesstree's establishment and spread. Early and late frosts and minimum winter temperatures apparently limit princesstree's establishment and spread in the United States [43,70,98,127,158]. In China, princesstree occurs south of the 32 °F (0 °C) isotherm [62,63] in areas that receive mean annual rainfall from 20 to 120 inches (500-3,000 mm) [37]. In the United States, it is typically not invasive in regions where temperatures drop below 32 °F (0 °C) for long periods [38,63,95,126]. USDA hardiness zones 7 to 10, where average annual minimum temperatures range from 0 to 40 °F (-18 to 4 °C) [72], are considered most favorable for princesstree [10].

When fully dormant, mature princesstrees can withstand temperatures as low as -13 °F (-25 °C), but individual plants are more susceptible to frost damage when actively growing or young and are damaged by 14 °F (-10 °C) or lower temperatures [37]. Damage to seeds by low temperatures is unknown, but seeds can be dry-stored at -4 °F (-20 °C) without losing viability [114]. Princesstree may be top-killed by low temperatures [13,37,48,81,98,126]. Following damage by cold, plants typically sprout [13,37,98,126]. In some cases flower buds are damaged by extreme cold, as observed by Braun [19] in Ohio. Thus, the reproductive potential of an individual can be greatly limited in cold climates even if individual trees survive. Predicted climate change might result in princesstree spreading beyond its current distribution, pushing altitudinal limits upwards and latitudinal limits northward of its current range [118].

Princesstree is an early-successional species that is intolerant of shade [53,90,147]. It possesses many characteristics often associated with early-successional species and invasive behavior: 1) copious production of small, wind-dispersed seeds, 2) rapid growth of seedlings, 3) strong shade intolerance and "poor competitive ability", 4) early age to first reproduction (<10 years), and 5) sprouting ability [63]. Apparently due to growth interference by neighboring vegetation and an inability to reproduce in shade, princesstree is a transient invader following disturbance [79].

Princesstree is frequently described as having "poor competitive ability", particularly during the first few years of age [4,12,14,16,34,37,52,63,138]. Many authors have demonstrated that treating neighboring vegetation with herbicides increases princesstree seedling survival and growth (e.g., [4,12,145]). However, the influence of neighboring vegetation on princesstree is variable. Hyatt and Casper [67] concluded that native Allegheny blackberry in an eastern Pennsylvania mixed-hardwood forest gap inhibited American pokeweed seed input and increased seed mortality (P<0.05); however, no significant effect on princesstree seed input, germination, or survival was observed [67].

Field observations in Illinois suggested that if other vegetation overtops and shades princesstree within the 1st year of establishment, princesstree survival may be low [4]. A shift in the distribution of princesstree seedling heights during the first 4 years following fire in the Linville Gorge Wilderness Area, North Carolina, suggested that surviving individuals were those that grew faster than and thus stayed above the regenerating vegetation or were in a location where regeneration of all vegetation was slow. The author surmised that although similar shifts occur in most species over time, the relative rapidity of the shift suggested that a lack of persistence of princesstree in some portions of the postfire landscape may be due to its "poor competitive ability" [79].

If princesstree seedlings grow fast enough to remain in the canopy, survival may be high. Seedlings over 5 feet (1.5 m) tall can create sufficient leaf surface area to shade out undergrowth [15]. Longbrake [90] concluded that once princesstree establishes, "competition will not hinder its invasive potential"; instead, light availability is apparently the dominant factor influencing its growth. Seedlings can acclimate to low light; however, growth is slower [91] and according to Zhu and others [158], around 70% shade may be fatal to princesstree saplings.
  Recovery of midsuccessional vegetation after disturbance may create unsuitable conditions for princesstree. Without repeated canopy-opening disturbance, princesstree is likely to remain suppressed in the understory [64,90]. It is rarely present in the canopy of mature forests [64,93]. Even if it persists in the tree canopy, the requirements of high light and bare soil for seed germination may lead to reproductive failure beneath the canopy of mature trees [64]. Hu [62] suggests that by the time Paulownia grows to maturity, the seeds it produces likely cannot survive within the same habitat as the parent plant because the succeeding vegetation has "modified the physical environment so much that no new Paulownia has any chance to get established". Thus, princesstree may not alter the successional pathways of some native ecosystems.

Relatively poor quality sites—for example, those with low fertility and frequent drought—may provide better survival for princesstree in the long term [4]. Over time in the Linville Gorge Wilderness Area, princesstree became increasingly limited to the most xeric portions of the landscape, such as slopes and ridgetops, where native plant regeneration was low. The distribution of princesstree 1 and 4 years after fire indicated that princesstree habitat contracted over this 4-year period; habitat losses were more concentrated on mesic sites, at relatively low elevations, and on relatively flat slopes. Princesstree was reduced mainly where fire severity was low, moisture availability was high, and native plants were regenerating well [79].
Princesstree in postfire habitat in Linville Gorge Wilderness Area, North Carolina. Photo by Dane Kuppinger.

The frequency and scale of disturbance may be important to establishment and persistence of princesstree [90]. Several reviews note that princesstree invasion of native forests may be primarily facilitated by large-scale disturbances, which are more likely to result in reduced interference from other vegetation, high light, and exposed mineral soil necessary for optimal establishment [24,144,146,147]. Establishment of princesstree in a streamside forest after Hurricane Camille peaked immediately following the hurricane and decreased over time. Sixteen years after the disturbance, no new individuals were recruited. The author attributed this to a lack of disturbance since the hurricane and overshading by native vegetation [146]. No new princesstrees were recruited 3 years after the initial postfire recruitment phase in Linville Gorge Wilderness Area. Approximately 5,000 acres (2,000 ha) of the Wilderness Area burned [111], with severity ranging from low-severity surface fire to high-severity crown fire [79]. Princesstree recruitment after postfire year 3 may have failed due to increased competition for light by regenerating native vegetation that limited germination of seeds after that time (see Impacts) [79]. Although frequent disturbance may sometimes promote establishment and spread of princesstree, there are exceptions. For example, princesstree established on sandy and silty bars of Plummers Island, Maryland, along with eastern cottonwood (Populus deltoides), green ash (Fraxinus pennsylvanica), southern catalpa (Catalpa bignonioides), sycamore, silver maple (Acer saccharinum), and boxelder (Acer negundo), but was rarely able to survive past the first year's growth because princesstree seedlings died when the bars flooded the following winter [117].


SPECIES: Paulownia tomentosa


    Princesstree in postfire habitat in Linville Gorge Wilderness Area, North Carolina. Photo by Dane Kuppinger.

Immediate fire effect on plant: The aboveground portion of princesstree is probably easily killed by fire. The brittle branches, thin, flaky bark, and large leaves with a high surface-to-volume ratio suggest that it has good potential for crowning fires; however, crowning fire behavior has not been reported for princesstree as of this writing (2009). Although princesstree roots are frequently shallow [4,10,29,62,63,130,158], even the most severe fires rarely damage plant tissues below 2 inches (10 cm) in the soil [119]; thus, many roots are probably insulated from heat damage by soil and likely survive low- to moderate-severity fire.

The effect of fire on seeds depends upon fire severity. In a laboratory experiment, Kuppinger [79] found a significant negative relationship between germination and the maximum temperature experienced by princesstree seeds (P<0.05). In this study, a series of "burn events" were simulated by placing seeds in a wire mesh bag at 3 depths (on the litter surface, on the soil surface, and buried at 0.8-inch (2 cm) depth) and exposing them to a range of fire temperatures (approximate range: 77-437 °F (25-225 °C)) for as long as 210 seconds. After the burn events, seeds were germinated in a greenhouse. Results showed that seeds were exposed to decreased temperatures with increasing soil depth, making princesstree seeds on the soil surface more vulnerable to fire-induced mortality than those in the soil. Less than 0.1% of seeds from all depths germinated when soil surface temperatures exceeded 212 °F (100 °C) [79]. Since soil surface temperatures during fire frequently exceed this (see [32] for a review), mortality of unburied princesstree seeds during wildfire is likely. This evidence suggests that princesstree seeds may only survive fire when buried, or if on the soil surface, when fires are of very low severity [79].

Postfire regeneration strategy [125]:
Tree with adventitious buds, a sprouting root crown, and root suckers
Geophyte, growing points deep in soil
Ground residual colonizer (on site, initial community)
Initial off-site colonizer (off site, initial community)
Secondary colonizer (on- or off-site seed sources)

Fire adaptations and plant response to fire: Highly shade-intolerant, princesstree requires large-scale disturbances such as fire, landslides, flood scour, or other land scarification for optimal stand establishment [63]. The small, wind-dispersed seeds germinate almost exclusively on open sites with exposed mineral soil [18,63]. These traits are similar to those of many native fire-dependent species, such as Table Mountain pine and pitch pine [148]. Princesstree may grow rapidly after fire. For example, in oak-pine forest in Linville Gorge Wilderness Area dominated by scarlet oak, chestnut oak, pitch pine, and Table Mountain pine, seedlings grew to 14 feet (4 m) tall 4 years after fire [40]. Furthermore, princesstree's ability to sprout from adventitious buds along its bole, root crown, and/or roots after partial to complete top-kill [63] likely allows it to persist after fire. Thus, prescribed fire meant to enhance regeneration and maintenance of native, fire-dependent forest species may also create conditions suitable for princesstree regeneration.

Establishment of princesstree after wildfires has been reported in the fire-dependent Table Mountain pine-pitch pine forests of the southern Appalachians (e.g., [40,84,111]). On the western rim of the Linville Gorge Wilderness Area, Dumas and others [40] examined the effects of a fall 2000 wildfire in primarily xeric oak-pine forest. This area had not been burned in 50 years and had succeeded to a mixed-hardwoods community with a dense mountain-laurel (Kalmia latifolia) understory [111]. Throughout Linville Gorge Wilderness Area, fire severity ranged from low-severity surface fire to high-severity crown fire (see Kuppinger [79] for more information). In this area, the fire was a low-severity surface fire, with crowning mainly restricted to stands of pitch pine and Table Mountain pine that had been killed by southern pine beetle. Two years after fire, little overstory mortality was evident in healthy stands. Most of the understory, composed primarily of mountain-laurel, was top-killed and had subsequently sprouted. The fire reduced surface organic horizons nearly 50% in burned plots relative to unburned plots and increased light penetration about 15%, resulting in greater soil temperature extremes but no differences in available nitrogen or phosphorus. Rates of soil respiration and litter decomposition tended to be lower in burned than unburned plots. This low-intensity surface fire caused postfire basal sprouting of trees and shrubs, increased species richness in the herb layer, and allowed the establishment of pitch pine and princesstree seedlings. Princesstree had not been detected in the 12,002-acre (4,857 ha) Wilderness Area prior to the fire, but seedlings had "rapidly increased in number and height" by postfire year 4 [40]. Potential brevity of princesstree seeds in the soil seed bank and susceptibility of seeds to fire-induced mortality suggests that princesstree may have established in the Linville Gorge Wilderness Area from seed dispersed after the fire rather than from dormant seed present in the soil seed bank prior to the fire (see Fire Management Considerations and Seed banking) [79,111].

Landscapes with high fire severity may provide quality habitat for princesstree [79]. Kuppinger [79] examined postfire establishment and spread by princesstree across 5 sites in western North Carolina and eastern Tennessee that burned in 2000 and 2001. Data collected in postfire years 1 and 4 were compared. General patterns emerged, including a positive association with relatively dry, upland reaches of the landscape, a negative association with remaining vegetation cover taller than 3.3 feet (1 m), and a negative association with decreasing hill shade.

Fire severity and intensity likely affect regeneration of princesstree. Because of variations in fuels and topography, fire creates a variety of microsites within each burned area. High-severity fire produces favorable conditions for princesstree germination and establishment but killing mature trees and some seeds, particularly those in the litter. Conversely, low-severity fire may not kill mature princesstree trees or their seeds but is less likely to create conditions necessary for germination and establishment. More information is needed about the establishment and persistence of princesstree seedlings and sprouts and their ability to compete with native vegetation after fire (see Successional Status) [144].

Fuels: Princesstree may increase fuel loads locally but may not increase fire hazard and thus not affect fire regimes. Princesstree's growth habit suggests that it may contribute substantially to fuel loads. Princesstrees may produce large amounts of litter. The brittle branches break easily even when green, and branch die-back from frost is common, so the branches, large leaves, and numerous seed capsules accumulate under the tree canopy (e.g., [37,81,115,126]). However, princesstree is not considered a fire hazard [44]. Paulownia wood has low thermal (0.063-0.086 Kcal m‾ ¹ hr‾ ¹ °C‾ ¹) and temperature conductivity (0.000561-0.000631 m‾ ¹ hr‾ ¹) and thus very high heat insulation properties and low combustibility relative to other species [158]. Relatively high moisture content and low ignitability of chemicals in the plant partially explain its low combustibility and consumption in fire. Li and Oda [87] studied the characteristics of princesstree wood in the laboratory and found that "the thermal conductivity of princesstree is lowest among all types of wood", although the authors did not provide relative numbers. The porous microstructure of princesstree wood and its chemical composition help explain its light weight, relatively low combustibility, and "flame retardant" characteristics compared to other types of wood [87]. For more information on the cellular structure and physical characteristics of princesstree wood see Zhu and others [158] and Hu [62,63].

Fire regimes: Little information is available on the fire regime of plant communities in princesstree's native habitat in China. Its ability to sprout and establish from off-site, wind-dispersed seeds, its rapid growth rate, early age to seed production, and appearance in early-successional plant communities in North America (see Habitat Types and Plant Communities) suggest that princesstree is tolerant of short fire-return intervals and stand-replacing disturbances. Lack of persistence in shaded sites suggests that long fire-return intervals are not favorable.

It is difficult to assess how princesstree may alter fire regimes in North American ecosystems and plant communities where it is present. Its low heat of combustion relative to other species suggests that its populations could possibly alter properties of the native fuel bed (see Fuels). Further information, especially on postfire response of princesstree, is needed to increase understanding of the effects of princesstree on fire regimes in North America. The Fire Regime Table summarizes characteristics of fire regimes for vegetation communities in which princesstree may occur. Find further fire regime information for the plant communities in which this species may occur by entering the species name in the FEIS home page under "Find Fire Regimes".

Because princesstree invades readily after disturbance, prescribed fire and fuels management activities may increase its populations. Thus, prescribed fire alone is not considered a control option for princesstree [44].

Princesstree may establish from the seed bank after fire. Viable princesstree seeds have been found in the soil seed bank of some forest communities (see Seed banking) [36,67], including the pine barrens region of southern New Jersey, where prescribed fire has been used since the 1930s [92]. However, princesstree seed mortality may be high after fire (see Immediate fire effect on plant), particularly, the "high severity fires most likely to produce the most suitable habitats for princesstree establishment" [79]. Thus, the establishment and spread of princesstree after fire may be primarily controlled by the yearly seed rain rather than an accumulation of seeds within the seed bank [79].

Preventing invasive plants from establishing in burned areas is the most effective and least costly management method. This may be accomplished through early detection and eradication, careful monitoring and follow-up, and limiting dispersal of invasive plant seed into burned areas. Evans and others [44] made the following management suggestions for preventing princesstree invasion after fire and fuels management activities. First, conduct control measures for princesstree before initiating silvicultural and/or prescribed fire treatment (see Control). This helps prevent mature trees from going to seed and reduces reproduction by sprouting. Second, plan late-season burns. Princesstree's response to fire depends upon the season fire occurs. Since seeds germinate in the first growing season following dispersal in the late summer and early fall if they encounter sufficient light levels and bare soil conditions, early spring fires are highly conducive to princesstree establishment and should be avoided [44]. Conversely, fire in the late summer and fall may kill seeds on the soil surface [79], possibly preventing princesstree establishment. Third, because seeds are easily transported, clean all equipment thoroughly before and after tree harvest, prescribed fire, or mechanical site preparation [44]. Fourth, because princesstree is promoted by activities that disturb the soil, monitor sites for new infestations whenever there is a nearby (<6 miles (10 km)) [79] seed source and follow up with additional control measures as needed. Particular attention should be paid to roadways, skid trails, and other disturbed grounds because these are likely corridors for invasion [44,84].

General recommendations for preventing invasive plants from establishing in weed-free burned areas include:

For more detailed information on these topics see the following publications: [6,20,50,139].


SPECIES: Paulownia tomentosa

Palatability/nutritional value: Domestic livestock and wildlife regularly consume princesstree leaves, flowers, and branches. In reviews, several authors mention the use of Paulownia leaves as fodder for domestic sheep, goats, pigs, and rabbits [29,34,37,74,78,149,158]. Leaves of 3 Paulownia species (P. tomentosa, P. fortunei, and P. elongata) were highly palatable to domestic goats in experimental studies and had "adequate" nutritional value for domestic goat browse as long as minerals were supplemented [108]. Leaves appear to be equally palatable to wildlife. High rates of herbivory were observed on young seedlings by unspecified burrowing animals and white-tailed deer in forest, edge, and clearcut habitats in Ohio [90]. Mitchem and others [98] suggested that white-tailed deer commonly browsed princesstree in Virginia. Little is known about princesstree seed predation, but field experiments in Ohio suggest that seed predation by wildlife may be minimal [90]. The rapid growth and coppicing ability of princesstree may allow it to establish despite heavy browsing pressure [74,91].

Cover value: No information is available on this topic.

Princesstree is valued in eastern Asia for its medicinal, ornamental, and timber uses [62,63]. In the United States, it has been widely planted as an ornamental (e.g., [41]), as a source of high-value export lumber (e.g., [10,26,57,96,106,130]), and for revegetation of land disturbed by coal mining (e.g., [143]). Except for its use as an ornamental, little attention was given to princesstree in the United States until the 1970s [58]. The United States began exporting princesstree wood to Japan in 1972. The logs obtained from wild-grown trees in the United States were of high quality, making prices for princesstree logs comparable to expensive native hardwoods such as black walnut (Juglans nigra) [57]. High prices encouraged interest in cultivating princesstree for timber production and led to much research regarding its cultivation on plantations and surface-mined lands [26,37,51,57,58,106,115,130,133]. Princesstree has since been extensively cultivated and grown in commercial plantations in the United States and throughout the world (see General Distribution) [96]. The commercial market for princesstree in the United States likely peaked in the late 1970s and early 1980s [58,106], when it was promoted as a "magic tree" [29] or as an "eco-friendly multi-purpose species" [34].

Frequent planting and increased propagule pressure may have resulted in increased invasibility of native communities by princesstree. The 1990s marked the first time that researchers and land managers began to see princesstree establish after fire in native xeric plant communities in the southern Appalachians [79]. Beginning in the early 1990s, focus in the literature gradually shifted from promotion to eradication of princesstree (see Impacts).

Wood products: The characteristics of princesstree wood make it suitable for a diversity of uses, and many reports have touted the unique physical and mechanical properties of princesstree wood (e.g., [38,58,62,63,106,115,123,130]). Its wood is used to make plywood and other house construction wood (other than for structural timber), paper, veneer, hand-carvings, clogs, musical instruments, furniture, and kitchen items such as rice pots, water pails, bowls, and spoons [34,37,51,57,62,63,78,106,115,133,138].

Reforestation and reclamation: Princesstree invades open, disturbed areas and often tolerates the harsh environmental conditions of surface mines [31]. Several studies have advocated using it for reclamation [25,26,31,95,130,136]. It has been planted on surface-mined lands throughout the eastern United States, including West Virginia, Kentucky, Tennessee, and Alabama [57,106,130,143]. However, several authors describe it as having limited importance for use in revegetation on coalmined sites due to the frequent difficulties of establishing princesstree relative to other species [129,133,143]. It was unclear how common the use of princesstree in reclamation was as of this writing (2009).

Agroforestry and cropping systems: The Chinese have developed intercropping and agroforestry systems for Paulownia, including princesstree, which have been evaluated extensively in the literature (e.g., [29,34,37,38,149,154]). Species of Paulownia other than princesstree are apparently preferred for these practices [74].

Impacts: Princesstree is a moderate to severe threat to native plant communities in many eastern states. In general, it is considered moderately invasive in native communities of the northeastern United States [137]. In the Southeast, it is typically considered a substantial or severe threat to native communities [1,47,75,80,120,121]. Princesstree is considered moderately invasive in Virginia [142]. In a study using the Southern Research Stations Forest Inventory and Analysis database, cover estimates of princesstree totaled over 20,000 acres in 12 southeastern states [97]:

Estimates of area covered by princesstree in the Southeast as of 2008 [97]
State Acres
Alabama 2,284
Arkansas 82
Florida 82
Georgia 347
Kentucky 2,726
Louisiana 7
Mississippi 1,867
North Carolina 2,297
South Carolina 95
Tennessee 7,361
Texas (east) Not detected
Virginia 6,331
Total acres covered 23,478

Princesstree is primarily a threat to native communities in heavily disturbed areas in the eastern United States. In the southern Appalachian Mountains it excludes native species in areas that experience frequent fire or in areas with naturally exposed soils and sunny aspects such as cliffs and rocky outcrops (see Site Characteristics) [70,84]. In the Great Smoky Mountains National Park and Linville Gorge Wilderness Area, its ability to colonize rocky or infertile sites makes it a threat to 2 rare, endangered species (Heller's blazing star (Liatris helleri), mountain goldenheather (Hudsonia montana)) that require these marginal habitats [44,79]. Its ability to sprout or establish by seed quickly after fire has allowed princesstree to replace native fire-dependent species such as Table Mountain pine and pitch pine in some areas of Great Smoky Mountains National Park [118].

Many studies report princesstree is of minor importance in intact forest and undisturbed environments [37]. For example, in New London County, Connecticut, it had increased in disturbed areas but had not spread to more mature plant associations; the remaining native terrestrial flora had not seriously declined despite a high percentage of nonnative species [59]. In western North Carolina and eastern Tennessee, there was no significant correlation between princesstree's presence or cover and native species cover or diversity; however, the author cautioned about the stability of this condition if princesstree cover were to increase [79]. Princesstree was not considered an "aggressive invader" in eastern forests lacking large-scale disturbance due to its habit of forming "small scattered populations in much the same way that it does in its natural environments in China" [147]. In China, Hu [63] speculated that the requirement for high light for germination and the small size of the seed—with little food reserve—probably contribute to the isolated occurrence of princesstrees there.

Kuppinger [79] concluded that princesstree in western North Carolina and eastern Tennessee "appears to be able to germinate and survive for a year or 2 across a much larger range of habitat conditions than will enable it to survive to maturity". The author continued by stating that "in situations where there is interest and resources for control efforts, (habitat models) indicate that control may be unnecessary over large portions of the landscape initially invaded by princesstree. In these areas, it is likely that regeneration of native vegetation will eventually exclude princesstree as it is apparently a poor competitor for space and light. Because of this, control efforts should be focused on the most xeric and exposed portions of the landscape where habitat models predict princesstree will persist and a high-light, low-competition environments will be maintained" [79].

Control: Princesstree control requires persistence due to its strong sprouting ability, rapid growth, and prolific seed production. Posttreatment monitoring and retreatment are essential. Treated areas should be checked once or more a year, with any new sprouts or seedlings retreated (cut, sprayed, or pulled) as soon as possible so that roots do not have time to build up carbohydrate reserves and grow larger. Princesstree's rapid root growth and sprouting ability underscore the need to eradicate seedlings when they are small and before they become established.

In all cases where invasive species are targeted for control, no matter what method is employed, the potential for other invasive species to fill their void must be considered [21]. Bean and others [10] review application methods for many of the control methods discussed below; however, the information provided herein is not intended to be either comprehensive or prescriptive in nature.

Fire: For information on the use of prescribed fire to control this species, see Fire Management Considerations.

Prevention: Managing to maintain the integrity of the native plant community and mitigate the factors enhancing ecosystem invasibility is likely to be more effective than managing solely to control the invader [60]. Maintaining high plant species richness in native communities is likely to decrease the invasibility of plant communities by princesstree because interference from neighboring vegetation may decrease princesstree's growth and survival (see Successional Status). Due to princesstree's preference for open, disturbed habitat, its establishment may be prevented by minimizing loss or disturbance of native communities [99,103]. For example, Williams [146] surmised that since light levels may be inadequate for the growth and survival of princesstree seedlings or sprouts, small forest gaps are unlikely to contribute to its population maintenance in most forests, whereas native early-successional forest trees such as yellow-poplar and black birch may occupy canopy gaps of various sizes [146]. Given this, planting of native species in the understory of existing stands may allow native species to increase while preventing princesstree germination [90].

Successful control of princesstree requires prevention of propagation and planting by restricting the sale and use of princesstree and increasing public education about its impacts on native communities. In 2006, Webster and others [144] stated that "a quick review of the forestry extension web sites of 24 land grant universities in the eastern United States revealed that 7 institutions still offer publications that promote invasive exotic woody plants for plantations, wildlife habitat improvement, and ornamental plantations". The authors suggest that the first step in preventing the introduction of princesstree is by "encouraging the use of native species in forestry and horticulture applications" [144].

Another method of preventing princesstree infestation is by developing and using a risk assessment model [35]. A risk assessment model combines information regarding current infestations with what is known about the species' biology. Land managers can then use the model to identify the probability of occurrence and areas at risk of invasion. Although a risk assessment model had not been developed for princesstree in the United States as of this writing (2009), McNab and Loftis [94] developed a model for oriental bittersweet (Celastrus orbiculatus) and suggested that such a model could be broadly applicable to princesstree and other invasive plants.

Weed prevention and control can be incorporated into many types of management plans, including those for logging and site preparation, grazing allotments, recreation management, research projects, road building and maintenance, and fire management [139]. See the Guide to noxious weed prevention practices for specific guidelines in preventing the spread of weed seeds and propagules under different management conditions.

Physical and/or mechanical: Mechanical methods can be an effective initial control measure for princesstree. Cut mature trees at ground level. To prevent seed production, cutting is most effective at the onset of flowering. Because princesstree spreads by suckering, root sprouts are common after treatment, and additional control methods such as repeated cutting for sprouts or an herbicidal control to prevent sprouting may be required [10]. Repeated cutting eventually exhausts the roots and kills the plant, but this may take several years [71]. Girdling kills the top of a tree but sprouts are common and may require a follow-up treatment with a foliar herbicide such as glyphosate or triclopyr. Seedlings can be controlled by hand-pulling; however, the entire root must be removed because broken root fragments may sprout [10].

Biological: Biocontrol could potentially reduce the invasiveness of princesstree in the United States [42], but no biocontrol methods are available as of this writing (2009). Ding and others [35] prioritized princesstree and 9 other species as targets for future biological control efforts based on information on their importance in introduced areas, availability of their host-specific insects or pathogens in China, and their potential biological control risk to introduced ecosystems. According to this study, princesstree has no congener species in the United States, making the potential biological control risk to introduced ecosystems low. Of 128 natural enemies in China, 19 may be potential biological control agents for use in the United States due to their narrow host ranges.

Biological control of invasive species has a long history that indicates many factors must be considered before using biological controls. Refer to these sources [141,151] and the Weed control methods handbook [135] for background information and important considerations for developing and implementing biological control programs.

In the United States, native and nonnative invertebrates, fungi, and diseases are known to adversely affect princesstree. Several studies have reported mortality of seedlings due to root rots [13,62,63,123,127,138]. Stringer [127] described 2 fungi (Rhizoctonia sp., Colletotrichum sp.) that infected seedlings and caused die-back in field experiments in Kentucky. Several foliage diseases causing at least superficial damage to princesstrees have been reported in the United States, including Phyllosticta paulowniae, Phyllactinia guttata, and Uncinula clintonii ([70], Hepting 1971, cited in [16]). Princesstree is subject to minor damage by the Comstock mealybug (Pseudococcus comstocki), an introduced species from Asia [138] and saltmarsh caterpillar (Estigmene acrea), a native species [15].

Chemical: Herbicides may provide initial control of a new invasion or a severe infestation but are rarely a complete or long-term solution to invasive species management [23]. Herbicides are more effective on large infestations when incorporated into long-term management plans that include replacement of weeds with desirable species, careful land use management, and prevention of new infestations. Following stem control, total elimination requires surveillance and treatment of root sprouts and plant germinants that originate from the soil seed bank [96]. Control with herbicides is temporary because it does not change conditions that allow infestations to occur [156]. See The Nature Conservancy's Weed control methods handbook [135] for consideration on the use of herbicides in wildlands and detailed information on specific chemicals.

According to reviews, systemic herbicides (e.g., triclopyr and glyphosate), which kill roots, currently provide the best chemical control for princesstree [10], although results may vary depending upon environmental conditions. These herbicides risk damage to nontarget species. When princesstree is interspersed with nontarget species, the foliage, stumps, or basal bark of individual trees can be treated with herbicides [10].

Integrated management: Princesstree can be controlled most effectively using integrated management. Cutting or girdling trees may prevent seed production. However, princesstree readily sprouts and repeated cutting or an herbicide treatment following cutting may be necessary [134]. Korostoff [77] reports that princesstree was eliminated in northwestern Pennsylvania by cutting followed by stump treatment with herbicide. Integrated management should include establishing desirable species in addition to considerations for killing the target plant.


SPECIES: Paulownia tomentosa

The following table provides fire regime information that may be relevant to princesstree habitats. Find further fire regime information for the plant communities in which this species may occur by entering the species name in the FEIS home page under "Find Fire Regimes".

Fire regime information on vegetation communities in which princesstree may occur. This information is taken from the LANDFIRE Rapid Assessment Vegetation Models [83], which were developed by local experts using available literature, local data, and/or expert opinion. This table summarizes fire regime characteristics for each plant community listed. The PDF file linked from each plant community name describes the model and synthesizes the knowledge available on vegetation composition, structure, and dynamics in that community. Cells are blank where information is not available in the Rapid Assessment Vegetation Model.
Southeast Great Lakes Northeast South-central US Southern Appalachians
Great Lakes
Vegetation Community (Potential Natural Vegetation Group) Fire severity* Fire regime characteristics
Percent of fires Mean interval
Minimum interval
Maximum interval
Great Lakes Grassland
Mosaic of bluestem prairie and oak-hickory Replacement 79% 5 1 8
Mixed 2% 260    
Surface or low 20% 2   33
Great Lakes Woodland
Northern oak savanna Replacement 4% 110 50 500
Mixed 9% 50 15 150
Surface or low 87% 5 1 20
Great Lakes Forested
Northern hardwood maple-beech-eastern hemlock Replacement 60% >1,000    
Mixed 40% >1,000    
Great Lakes floodplain forest
Mixed 7% 833    
Surface or low 93% 61    
Maple-basswood Replacement 33% >1,000    
Surface or low 67% 500    
Maple-basswood mesic hardwood forest (Great Lakes) Replacement 100% >1,000 >1,000 >1,000
Maple-basswood-oak-aspen Replacement 4% 769    
Mixed 7% 476    
Surface or low 89% 35    
Oak-hickory Replacement 13% 66 1  
Mixed 11% 77 5  
Surface or low 76% 11 2 25
Vegetation Community (Potential Natural Vegetation Group) Fire severity* Fire regime characteristics
Percent of fires Mean interval
Minimum interval
Maximum interval
Northeast Woodland
Eastern woodland mosaic Replacement 2% 200 100 300
Mixed 9% 40 20 60
Surface or low 89% 4 1 7
Rocky outcrop pine (Northeast) Replacement 16% 128    
Mixed 32% 65    
Surface or low 52% 40    
Pine barrens Replacement 10% 78    
Mixed 25% 32    
Surface or low 65% 12    
Oak-pine (eastern dry-xeric) Replacement 4% 185    
Mixed 7% 110    
Surface or low 90% 8    
Northeast Forested
Northern hardwoods (Northeast) Replacement 39% >1,000    
Mixed 61% 650    
Eastern white pine-northern hardwoods Replacement 72% 475    
Surface or low 28% >1,000    
Northern hardwoods-eastern hemlock Replacement 50% >1,000    
Surface or low 50% >1,000    
Northern hardwoods-spruce Replacement 100% >1,000 400 >1,000
Appalachian oak forest (dry-mesic) Replacement 2% 625 500 >1,000
Mixed 6% 250 200 500
Surface or low 92% 15 7 26
Beech-maple Replacement 100% >1,000    
South-central US
Vegetation Community (Potential Natural Vegetation Group) Fire severity* Fire regime characteristics
Percent of fires Mean interval
Minimum interval
Maximum interval
South-central US Grassland
Oak savanna Replacement 3% 100 5 110
Mixed 5% 60 5 250
Surface or low 93% 3 1 4
South-central US Woodland
Oak-hickory savanna Replacement 1% 227    
Surface or low 99% 3.2    
Interior Highlands dry oak/bluestem woodland and glade Replacement 16% 25 10 100
Mixed 4% 100 10  
Surface or low 80% 5 2 7
Oak woodland-shrubland-grassland mosaic Replacement 11% 50    
Mixed 56% 10    
Surface or low 33% 17    
Interior Highlands oak-hickory-pine Replacement 3% 150 100 300
Surface or low 97% 4 2 10
Pine bluestem Replacement 4% 100    
Surface or low 96% 4    
South-central US Forested
Interior Highlands dry-mesic forest and woodland Replacement 7% 250 50 300
Mixed 18% 90 20 150
Surface or low 75% 22 5 35
Gulf Coastal Plain pine flatwoods Replacement 2% 190    
Mixed 3% 170    
Surface or low 95% 5    
West Gulf Coastal plain pine (uplands and flatwoods) Replacement 4% 100 50 200
Mixed 4% 100 50  
Surface or low 93% 4 4 10
West Gulf Coastal Plain pine-hardwood woodland or forest upland Replacement 3% 100 20 200
Mixed 3% 100 25  
Surface or low 94% 3 3 5
Southern floodplain Replacement 42% 140    
Surface or low 58% 100    
Southern floodplain (rare fire) Replacement 42% >1,000    
Surface or low 58% 714    
Southern Appalachians
Vegetation Community (Potential Natural Vegetation Group) Fire severity* Fire regime characteristics
Percent of fires Mean interval
Minimum interval
Maximum interval
Southern Appalachians Grassland
Bluestem-oak barrens Replacement 46% 15    
Mixed 10% 69    
Surface or low 44% 16    
Eastern prairie-woodland mosaic Replacement 50% 10    
Mixed 1% 900    
Surface or low 50% 10    
Southern Appalachians Woodland
Appalachian shortleaf pine Replacement 4% 125    
Mixed 4% 155    
Surface or low 92% 6    
Table Mountain-pitch pine Replacement 5% 100    
Mixed 3% 160    
Surface or low 92% 5    
Oak-ash woodland Replacement 23% 119    
Mixed 28% 95    
Surface or low 49% 55    
Southern Appalachians Forested
Bottomland hardwood forest Replacement 25% 435 200 >1,000
Mixed 24% 455 150 500
Surface or low 51% 210 50 250
Mixed mesophytic hardwood Replacement 11% 665    
Mixed 10% 715    
Surface or low 79% 90    
Appalachian oak-hickory-pine Replacement 3% 180 30 500
Mixed 8% 65 15 150
Surface or low 89% 6 3 10
Eastern hemlock-eastern white pine-hardwood Replacement 17% >1,000 500 >1,000
Surface or low 83% 210 100 >1,000
Oak (eastern dry-xeric) Replacement 6% 128 50 100
Mixed 16% 50 20 30
Surface or low 78% 10 1 10
Appalachian Virginia pine Replacement 20% 110 25 125
Mixed 15% 145    
Surface or low 64% 35 10 40
Appalachian oak forest (dry-mesic) Replacement 6% 220    
Mixed 15% 90    
Surface or low 79% 17    
Vegetation Community (Potential Natural Vegetation Group) Fire severity* Fire regime characteristics
Percent of fires Mean interval
Minimum interval
Maximum interval
Southeast Grassland
Southeast Gulf Coastal Plain Blackland prairie and woodland Replacement 22% 7    
Mixed 78% 2.2    
Southeast Woodland
Longleaf pine/bluestem Replacement 3% 130    
Surface or low 97% 4 1 5
Longleaf pine (mesic uplands) Replacement 3% 110 40 200
Surface or low 97% 3 1 5
Longleaf pine-Sandhills prairie Replacement 3% 130 25 500
Surface or low 97% 4 1 10
Southeast Forested
Coastal Plain pine-oak-hickory Replacement 4% 200    
Mixed 7% 100      
Surface or low 89% 8    
Loess bluff and plain forest Replacement 7% 476    
Mixed 9% 385    
Surface or low 85% 39    
Southern floodplain Replacement 7% 900    
Surface or low 93% 63    
*Fire Severities
Replacement: Any fire that causes greater than 75% top removal of a vegetation-fuel type, resulting in general replacement of existing vegetation; may or may not cause a lethal effect on the plants.
Mixed: Any fire burning more than 5% of an area that does not qualify as a replacement, surface, or low-severity fire; includes mosaic and other fires that are intermediate in effects.
Surface or low: Any fire that causes less than 25% upper layer replacement and/or removal in a vegetation-fuel class but burns 5% or more of the area [56,82].

Paulownia tomentosa: REFERENCES

1. Alabama Invasive Plant Council. 2007. List of Alabama's invasive plants by land-use and water-use sectors. Alabama Invasive Plant Council (Producer). Available: [2009, January 5]. [72714]
2. Allard, H. A.; Leonard, E. C. 1943. The vegetation and floristics of Bull Run Mountain, Virginia. Castanea. 8(1/3): 1-64. [72123]
3. Armstrong, Joseph E. 1985. The delimitation of Bignoniaceae and Scrophulariaceae based on floral anatomy and the placement of problem genera. American Journal of Botany. 72(5): 755-766. [72107]
4. Arnold, Lester E.; Gertner, George Z. 1988. Establishing zero-till Paulownia in permanent pastures with delayed herbicide application. Forestry Research Report No. 88-4. Urbana-Champaign, IL: University of Illinois, Department of Forestry; Illinois Agricultural Experiment Station. 5 p. [72780]
5. Arnold, Lester E.; Gertner, George Z. 1988. Field scale Paulownia management trials: first year results. Forestry Research Report No. 88-6. Urbana-Champaign, IL: University of Illinois, Department of Forestry; Illinois Agricultural Experiment Station. 7 pp. [72036]
6. Asher, Jerry; Dewey, Steven; Olivarez, Jim; Johnson, Curt. 1998. Minimizing weed spread following wildland fires. Proceedings, Western Society of Weed Science. 51: 49. [40409]
7. Barnhill, M. A.; Cunningham, M.; Farmer, R. E. 1982. Germination characteristics of Paulownia tomentosa. Seed Science and Technology. 10(2): 217-221. [72037]
8. Baron, Jill; Dombrowski, Christine; Bratton, Susan Power. 1975. The status of five exotic woody plants in the Tennessee District, Great Smoky Mountains National Park. NPS-SER Research/Resources Management Report No. 2. Gatlinburg, TN: Great Smoky Mountains National Park, Uplands Field Resarch Laboratory, Twin Creeks Area; Atlanta, GA: U.S. Department of the Interior, National Park Service, Southeast Region. 26 p. [72010]
9. Baskin, Carol C.; Baskin, Jerry M. 2001. Seeds: ecology, biogeography, and evolution of dormancy and germination. San Diego, CA: Academic Press. 666 p. [60775]
10. Bean, Ellen; McClellan, Linnea, tech. eds. 1996. Tennessee exotic plant management manual, [Online]. Southeast Exotic Pest Plant Council (Producer). Available: [2009, March 23]. [46442]
11. Beck, John T.; Van Horn, Gene S. 2007. The vascular flora of Prentice Cooper State Forest and Wildlife Management Area, Tennessee. Castanea. 72(1): 15-44. [72483]
12. Beckjord, P. R.; Melhuish, J. H., Jr.; Kundt, J. F. 1985. Survival and growth of Paulownia seedlings are enhanced through weed control. Journal of Environmental Horticulture. 3: 115-117. [72629]
13. Beckjord, Peter R. 1982. Containerized and nursery production of Paulownia tomentosa. Tree Planters' Notes. 33: 29-33. [72744]
14. Beckjord, Peter R. 1984. Paulownia tomentosa: a brief guide for the tree farmer. Miscellaneous Publication No. 984. College Park, MD: University of Maryland; Maryland Agricultural Experiment Station. 13 p. [Contribution No. 6648 of the Maryland Agricultural Experiment Station]. [72296]
15. Beckjord, Peter R.; McIntosh, Marla S. 1983. Paulownia tomentosa: effects of fertilization and coppicing in plantation establishment. Southern Journal of Applied Forestry. 7(2): 81-85. [72039]
16. Bonner, F. T. 1990. Paulownia tomentosa (Thunb.) Sieb. & Zucc. ex Steud. royal paulownia. In: Burns, Russell M.; Honkala, Barbara H., technical coordinators. Silvics of North America. Volume 2. Hardwoods. Agric. Handb. 654. Washington, DC: U.S. Department of Agriculture, Forest Service: 501-502. [73192]
17. Bonner, Franklin T. [In Press]. Paulownia tomentosa (Thunb.) Siev. & Zucc.--royal paulownia, [Online]. In: Bonner, Franklin T.; Nisley, Rebecca G.; Karrfait, R. P.; coords. Woody plant seed manual. Agric. Handbook 727. Washington, DC: U.S. Department of Agriculture, Forest Service (Producer). Available: http// [2009, February 5]. [72951]
18. Borthwick, H. A.; Toole, E. H.; Toole, V. K. 1964. Phytochrome control of Paulownia seed germination. Israel Journal of Botany. 13: 122-133. [72632]
19. Braun, E. Lucy. 1989. The woody plants of Ohio. Columbus, OH: Ohio State University Press. 362 p. [12914]
20. Brooks, Matthew L. 2008. Effects of fire suppression and postfire management activities on plant invasions. In: Zouhar, Kristin; Smith, Jane Kapler; Sutherland, Steve; Brooks, Matthew L., eds. Wildland fire in ecosystems: Fire and nonnative invasive plants. Gen. Tech. Rep. RMRS-GTR-42-vol. 6. Ogden, UT: U.S. Department of Agriculture, Forest Service, Rocky Mountain Research Station: 269-280. [70909]
21. Brooks, Matthew L.; Pyke, David A. 2001. Invasive plants and fire in the deserts of North America. In: Galley, Krista E. M.; Wilson, Tyrone P., eds. Proceedings of the invasive species workshop: The role of fire in the control and spread of invasive species; Fire conference 2000: 1st national congress on fire ecology, prevention, and management; 2000 November 27 - December 1; San Diego, CA. Misc. Publ. No. 11. Tallahassee, FL: Tall Timbers Research Station: 1-14. [40491]
22. Bryant, William S. 1993. Vegetation of loess bluff ravines in the Jackson Purchase Region of Kentucky. In: Gillespie, Andrew R.; Parker, George R.; Pope, Phillip E., eds. Proceedings, 9th central hardwood forest conference; 1993 March 8-10; West Lafayette, IN. Gen. Tech. Rep. NC-161. St. Paul, MN: U.S. Department of Agriculture, Forest Service, North Central Forest Experiment Station: 281-288. [27014]
23. Bussan, Alvin J.; Dyer, William E. 1999. Herbicides and rangeland. In: Sheley, Roger L.; Petroff, Janet K., eds. Biology and management of noxious rangeland weeds. Corvallis, OR: Oregon State University Press: 116-132. [35716]
24. Carpenter, S. B.; Immel, M. J.; Smith, N. D. 1983. Effect of photoperiod on the growth and photosynthetic capacity of Paulownia seedlings. Castanea. 48: 13-18. [72721]
25. Carpenter, Stanley B. 1977. This "princess" heals disturbed land. American Forests. 83: 22-23. [72633]
26. Carpenter, Stanley B.; Graves, Donald H. 1979. Paulownia: A valuable new timber resource. FOR-11. Lexington, KY: University of Kentucky, College of Agriculture, Cooperative Extention Service. 7 p. [72752]
27. Carpenter, Stanley B.; Smith, Naomi D. 1979. Germination of Paulownia seeds after stratification and dry storage. Tree Planters' Notes. 30(4): 4-6. [72043]
28. Carpenter, Stanley B.; Smith, Naomi D. 1981. Germination of Paulownia seeds in the presence and absence of light. Tree Planters' Notes. 32(4): 27-29. [72042]
29. Chong, Yinong. 1989. Paulownia: The rediscovery of China's "magic tree". Agroforestry Today. 1: 19-20. [72628]
30. Csurches, S.; Edwards, R. 1998. Potential environmental weeds in Australia: Candidate species for preventative control. Canberra, ACT: Biodiversity Group, Environment Australia. 202 p. Available online at [2009, January 9]. [72764]
31. Cunningham, Thomas R.; Carpenter, Stanley B. 1980. The effect of diammonium phosphate fertilizer on the germination of Paulownia tomentosa seeds. Tree Planters' Notes. 31: 6-8. [72598]
32. DeBano, Leonard F.; Neary, Daniel G.; Ffolliott, Peter F. 2005. [revised 2008]. Soil physical properties. In: Neary, Daniel G.; Ryan, Kevin C.; DeBano, Leonard F., eds. Wildland fire in ecosystems: effects of fire on soil and water. Gen. Tech. Rep. RMRS-GTR-42-vol. 4. Ogden, UT: U.S. Department of Agriculture, Forest Service, Rocky Mountain Research Station: 29-52. [55886]
33. DeLoach, C. Jack. 1997. Biological control of weeds in the United States and Canada. In: Luken, James O.; Thieret, John W., eds. Assessment and management of plant invasions. New York: Springer-Verlag: 172-194. [38164]
34. Dhiman, R. C. 1997. An eco-friendly multi-purpose species: Paulownia. MFP News. Uttaranchal, India: Minor Forest Products. 7(4): 14-16. [72044]
35. Ding, Jianqing; Reardon, Richard; Wu, Yun; Zheng, Hao; Fu, Weidong. 2006. Biological control of invasive plants through collaboration between China and the United States of America: a perspective. Biological Invasions. 8(7): 1439-1450. [71691]
36. Dobberpuhl, J. 1980. Seed banks of forest soils in east Tennessee. Knoxville, TN: University of Tennessee. 219 p. Thesis. [46755]
37. Donald, D. G. M. 1990. Paulownia--the tree of the future? South African Forestry Journal. 154: 94-98. [72045]
38. Dong, H.; van Buijtenen, J. P. 1994. A Paulownia seed source trial in east Texas and its implications to species introduction. Southern Journal of Applied Forestry. 18(2): 65-67. [72047]
39. Drake, Sara J.; Weltzin, Jake F.; Parr, Patricia D. 2003. Assessment of non-native invasive plant species on the United States Department of Energy Oak Ridge National Environmental Research Park. Castanea. 68(1): 15-30. [49846]
40. Dumas, Shay; Neufeld, Howard S.; Fisk, Melany C. 2007. Fire in a thermic oak-pine forest in Linville Gorge Wilderness Area, North Carolina: importance of the shrub layer to ecosystem response. Castanea. 72(2): 92-104. [72033]
41. Duncan, Wilbur H.; Duncan, Marion B. 1988. Trees of the southeastern United States. Athens, GA: The University of Georgia Press. 322 p. [12764]
42. Ehrenfeld, Joan G. 2008. Exotic invasive species in urban wetlands: environmental correlates and implications for wetland management. Journal of Applied Ecology. 45(4): 1160-1169. [71129]
43. Essl, Franz. 2007. From ornamental to detrimental? The incipient invasion of central Europe by Paulownia tomentosa. Preslia. 79(4): 377-389. [72048]
44. Evans, C. W.; Moorhead, D. J.; Bargeron, C. T.; Douce, G. K. 2006. Invasive plant responses to silvicultural practices in the South. Bugwood Network BW-2006-03. Tifton, GA: The University of Georgia, Bugwood Network. 52 p. Available online at [72425]
45. Fernald, Merritt Lyndon. 1950. Gray's manual of botany. [Corrections supplied by R. C. Rollins]. Portland, OR: Dioscorides Press. 1632 p. (Dudley, Theodore R., gen. ed.; Biosystematics, Floristic & Phylogeny Series; vol. 2). [14935]
46. Fitzgerald, Judith M.; Loeb, Robert E. 2008. Historical ecology of Inwood Hill Park, Manhattan, New York. The Journal of the Torrey Botanical Society. 135(2): 281-293. [72480]
47. Georgia Exotic Pest Plant Council. 2006. List of non-native invasive plants in Georgia, [Online]. Southeast Exotic Pest Plant Council (Producer). Available: [2009, January 5]. [72787]
48. Geyer, Wayne A. 2000. Paulownia tree trials in eastern Kansas. Transactions of the Kansas Academy of Science. 103(1/2): 95-97. [72106]
49. Gleason, Henry A.; Cronquist, Arthur. 1991. Manual of vascular plants of northeastern United States and adjacent Canada. 2nd ed. New York: New York Botanical Garden. 910 p. [20329]
50. Goodwin, Kim; Sheley, Roger; Clark, Janet. 2002. Integrated noxious weed management after wildfires. EB-160. Bozeman, MT: Montana State University, Extension Service. 46 p. Available online: [2003, October 1]. [45303]
51. Graves, Donald H. 1989. Paulownia: a potential alternative crop for Kentucky. FOR-11. Lexington, KY: University of Kentucky, College of Agriculture; Kentucky University Cooperative Extension Service. 5 p. [72781]
52. Graves, Donald H.; Stringer, Jeffrey W. 1989. Paulownia: a guide to establishment and cultivation. FOR-39. Lexington, KY: University of Kentucky, College of Agriuculture; Kentucky University Cooperative Extension Service. 6 p. [72053]
53. Grime, J. P. 1965. Shade tolerance in flowering plants. Nature. 28(5006): 161-163. [46122]
54. Grubisic, Dragoljub; Konjevic, Radomir. 1992. Light and temperature action in germination of seeds of the empress tree (Paulownia tomentosa). Physiologia Plantarum. 86(3): 479-483. [72055]
55. Grubisic, Dragoljub; Neskovic, Mirjana; Konjevic, Radomir. 1985. Changes in light sensitivity of Paulownia tomentosa and P. forunei seeds. Plant Science. 39(1): 13-16. [72056]
56. Hann, Wendel; Havlina, Doug; Shlisky, Ayn; [and others]. 2008. Interagency fire regime condition class guidebook. Version 1.3, [Online]. In: Interagency fire regime condition class website. U.S. Department of Agriculture, Forest Service; U.S. Department of the Interior; The Nature Conservancy; Systems for Environmental Management (Producer). 119 p. Available: [2008, September 03]. [70966]
57. Hardie, Ian; Kundt, John; Miyaska, Emiko. 1989. Economic feasibility of U.S. Paulownia plantations. Journal of Forestry. 87: 19-24. [72630]
58. Hemmerly, Thomas E. 1989. New commercial tree for Tennessee: princess tree, Paulownia tomentosa Steud. (Scrophulariaceae). Journal of the Tennessee Academy of Science. 64(1): 5-8. [72057]
59. Hill, Steven R. 1996. The flora of Latimer Point and vicinity, New London County, Connecticut. Rhodora. 98(894): 180-216. [44935]
60. Hobbs, Richard J.; Humphries, Stella E. 1995. An integrated approach to the ecology and management of plant invasions. Conservation Biology. 9(4): 761-770. [44463]
61. Howlett, Duncan. 1975. Forestry in the future of Brazil. American Forests. 81(11): 14-17; 44-45. [72724]
62. Hu, Shiu-Ying. 1959. A monograph of the genus Paulownia. Quarterly Journal of the Taiwan Museum. 12(1-2): 1-54. [72600]
63. Hu, Shiu-Ying. 1961. The economic botany of the Paulownias. Economic Botany. 15(1): 11-27. [72104]
64. Hull, James C.; Scott, Ralph C. 1982. Plant succession on debris avalanches of Nelson County, Virginia. Castanea. 47(2): 158-176. [41715]
65. Hunter, Carl G. 1989. Trees, shrubs, and vines of Arkansas. Little Rock, AR: The Ozark Society Foundation. 207 p. [21266]
66. Hyatt, Laura A. 1999. Differences between seed bank composition and field recruitment in a temperate zone deciduous forest. The American Midland Naturalist. 142(1): 31-38. [72109]
67. Hyatt, Laura A.; Casper, Brenda B. 2000. Seed bank formation during early secondary succession in a temperate deciduous forest. Journal of Ecology. 88(3): 516-527. [35772]
68. Immel, M. J.; Tackett, E. M.; Carpenter, S. B. 1980. Paulownia seedlings respond to increased daylength. Tree Planters' Notes. 31: 3-5. [72774]
69. Jia, Hui-jun; Ingestad, Torsten. 1984. Nutrient requirements and stress response of Populus simonii and Paulownia tomentosa. Physiologia Plantarum. 62(2): 117-124. [72065]
70. Johnson, James E.; Mitchem, David O.; Kreh, Richard E. 2003. Establishing royal paulownia on the Virginia Piedmont. New Forests. 25(1): 11-23. [72066]
71. Johnson, Kristine. 1996. Paulownia tomentosa--princess tree. In: Randall, John M.; Marinelli, Janet, eds. Invasive plants: Weeds of the global garden. Handbook #149. Brooklyn, NY: Brooklyn Botanic Garden: 38. [72851]
72. Jordan, Ramon. 2001. USDA plant hardiness zone map, [Online]. Washington, DC: U.S. Department of Agriculture, Agricultural Research Service, National Arboretum (Producer). Web version of: 1990 USDA plant hardiness zone map. Miscellaneous Publication No. 1475. Available: [2004, August 30]. [48600]
73. Kartesz, John T. 1999. A synonymized checklist and atlas with biological attributes for the vascular flora of the United States, Canada, and Greenland. 1st ed. In: Kartesz, John T.; Meacham, Christopher A. Synthesis of the North American flora (Windows Version 1.0), [CD-ROM]. Chapel Hill, NC: North Carolina Botanical Garden (Producer). In cooperation with: The Nature Conservancy; U.S. Department of Agriculture, Natural Resources Conservation Service; U.S. Department of the Interior, Fish and Wildlife Service. [36715]
74. Kays, Jonathan; Johnson Dale; Stringer, Jeffrey. 1998. How to produce and market paulownia. Cooperative Extension Bulletin 319. College Park, MD: University of Maryland. 22 p. [72771]
75. Kentucky Exotic Pest Plant Council. 2008. Invasive exotic plant list, [Online]. Southeast Exotic Pest Plant Council (Producer). Available: [2009, January 5]. [72785]
76. Knoepp, Jennifer D.; DeBano, Leonard F.; Neary, Daniel G. 2005. [revised 2008]. Soil chemistry. In: Neary, Daniel G.; Ryan, Kevin C.; DeBano, Leonard F., eds. Wildland fire in ecosystems: Effects of fire on soil and water. Gen. Tech. Rep. RMRS-GTR-42-vol. 4. Ogden, UT: U.S. Department of Agriculture, Forest Service, Rocky Mountain Research Station: 53-72. [55887]
77. Korostoff, Neil P. 1990. Urban ecosystem restoration: the case of the forested urban stream valley park. In: Hughes, H. Glenn; Bonnicksen, Thomas M., eds. Restoration '89: the new management challenge: Proceedings, 1st annual meeting of the Society for Ecological Restoration; 1989 January 16-20; Oakland, CA. Madison, WI: The University of Wisconsin Arboretum; Society for Ecological Restoration: 110-124. [14692]
78. Kukadia, M. U. 1996. Kiri (Paulownia tomentosa Steud.): a miracle tree. Indian Journal of Forestry. 19(2): 194-195. [72068]
79. Kuppinger, Dane Mitchell. 2008. Post-fire vegetation dynamics and the invasion of Paulownia tomentosa in the southern Appalachians. Chapel Hill, NC: University of North Carolina at Chapel Hill. 210 p. Dissertation. [72298]
80. Kuppinger, Dane. 2000. Management of plant invasions in the southern Appalachians. Chinquapin. 8(3): 21. [51456]
81. Kuser, John E.; Fimbel, Robert A. 1990. Preliminary evidence of genetic variation in winter injury and seedling height of paulownia trees in New Jersey. Tree Planters' Notes. 41(2): 31-33. [72069]
82. LANDFIRE Rapid Assessment. 2005. Reference condition modeling manual (Version 2.1), [Online]. In: LANDFIRE. Cooperative Agreement 04-CA-11132543-189. Boulder, CO: The Nature Conservancy; U.S. Department of Agriculture, Forest Service; U.S. Department of the Interior (Producers). 72 p. Available: [2007, May 24]. [66741]
83. LANDFIRE Rapid Assessment. 2007. Rapid assessment reference condition models, [Online]. In: LANDFIRE. U.S. Department of Agriculture, Forest Service, Rocky Mountain Research Station, Fire Sciences Lab; U.S. Geological Survey; The Nature Conservancy (Producers). Available: [2008, April 18] [66533]
84. Langdon, Keith R.; Johnson, Kristine D. 1994. Additional notes on invasiveness of Paulownia tomentosa in natural areas. Natural Areas Journal. 14(2): 139-140. [72100]
85. Leck, Mary Allessio; Leck, Charles F. 2005. Vascular plants of a Delaware River tidal freshwater wetland and adjacent terrestrial areas: seed bank and vegetation comparisons of reference and constructed marshes and annotated species list. Journal of the Torrey Botanical Society. 132(2): 323-354. [60627]
86. Leck, Mary Allessio; Simpson, Robert L. 1995. Ten-year seed bank and vegetation dynamics of a tidal freshwater marsh. American Journal of Botany. 82(12): 1547-1557. [26046]
87. Li, Peng; Oda, Juhachi. 2007. Flame retardancy of Paulownia wood and its mechanism. Journal of Materials Science. 42(20): 8544-8550. [72101]
88. Loeb, Robert E. 1986. Plant communities of Inwood Hill Park, New York County, New York. Bulletin of the Torrey Botanical Club. 113(1): 46-52. [62583]
89. Loftis, David L. 1978. Preharvest herbicide control of undesirable vegetation in southern Appalachian hardwoods. Southern Journal of Applied Forestry. 2(2): 51-54. [10632]
90. Longbrake, A. Christina W. 2001. Ecology and invasive potential of Paulownia tomentosa (Scrophulariaceae) in a hardwood forest landscape. Athens, OH: Ohio University. 174 p. Dissertation. [72300]
91. Longbrake, A. Christina W.; McCarthy, Brian C. 2001. Biomass allocation and resprouting ability of princess tree (Paulownia tomentosa: Scrophulariaceae) across a light gradient. The American Midland Naturalist. 146(2): 388-403. [72075]
92. Matlack, Glenn R.; Good, Ralph E. 1990. Spatial heterogeneity in the soil seed bank of a mature coastal plain forest. Bulletin of the Torrey Botanical Club. 117(2): 143-152. [22905]
93. McDonald, Robert I.; Urban, Dean L. 2006. Edge effects on species composition and exotic species abundance in the North Carolina Piedmont. Biological Invasions. 8: 1049-1060. [68821]
94. McNab, W. Henry; Loftis, David L. 2002. Probability of occurrence and habitat features for oriental bittersweet in an oak forest in the southern Appalachian Mountains, USA. Forest Ecology and Management. 155: 45-54. [40732]
95. Melhuish, J. H., Jr.; Gentry, C. E.; Beckjord, P. R. 1990. Paulownia tomentosa seedling growth at differing levels of pH, nitrogen, and phosphorus. Journal of Environmental Horticulture. 8(4): 205-207. [72077]
96. Miller, James H. 2003. Nonnative invasive plants of southern forests: A field guide for identification and control. Gen. Tech. Rep. SRS-62. Asheville, NC: U.S. Department of Agriculture, Forest Service, Southern Research Station. 93 p. Available online at [2004, December 10]. [50788]
97. Miller, James H.; Chambliss, Erwin B.; Oswalt, Christopher M. 2008. Estimated acres covered by the 33 nonnative invasive plants species in a state and Southern Region, [Online]. In: Maps of occupation and estimates of acres covered by nonnative invasive plants in southern forests using SRS FIA data posted on March 15, 2008. Athens, GA: University of Georgia, Bugwood Network; Washington, DC: U.S. Department of Agriculture, Forest Service; Animal and Plant Inspection Service, Plant Protection and Quarantine (Producers). Available: [2009, January 15]. [72772]
98. Mitchem, David O.; Johnson, James E.; Kreh, Richard E. 2002. Response of planted royal paulownia to weed control treatments after coppice. In: Outcalt, Kenneth W., ed. Proceedings, 11th biennial southern silvicultural research conference; 2001 March 20-22; Knoxville, TN. Gen. Tech. Rep. SRS-48. Asheville, NC: U.S. Department of Agriculture, Forest Service, Southern Research Station: 276-278. [72079]
99. Moore, James E. 2006. Effects of soil type and soil moisture on the germination and establishment of exotic and native trees of the North Carolina Piedmont. Greensboro, NC: The University of North Carolina. 48 p. Thesis. [72014]
100. Mueller, J. P.; Luginbuhl, J.-M.; Bergmann, B. A. 2001. Establishment and early growth characteristics of six Paulownia genotypes for goat browse in Raleigh, NC, USA. Agroforestry Systems. 52(1): 63-72. [72081]
101. Niemeier, Jean. 1984. I had to kill the empress. University of Washington Arboretum Bulletin. 47(2): 21-23. [72085]
102. Orians, G. H.. 1986. Site characteristics favoring invasions. In: Mooney, Harold A.; Drake, James A., eds. Ecology of biological invasions of North America and Hawaii. Ecological Studies 58. New York: Springer-Verlag: 133-148. [17513]
103. Pearson, Scott M.; Turner, Monica G.; Drake, Jason B. 1999. Landscape change and habitat availability in the Southern Appalachian Highlands and Olympic Peninsula. Ecological Applications. 9(4): 1288-1304. [72117]
104. Pennell, Francis W. 1919. Scrophulariaceae of the southeastern United States. Proceedings of the Academy of Natural Sciences of Philadelphia. 71(3): 224-291. [72108]
105. Pollio, Carol A.; Davidson, Walter H. 1992. Native seed bank: Brooklyn reclamation project. Park Science. 12(1): 10-11. [17787]
106. Preston, Dickson J. 1983. Paulownia: a miracle tree or a passing fancy? Forests. 89(5): 15-19, 47-52. [72782]
107. Racine, Charles H.; Hardin, James W. 1975. The vascular flora and vegetation in the Green River Gorge, North Carolina. Castanea. 40(4): 319-345. [72119]
108. Radford, Albert E.; Ahles, Harry E.; Bell, C. Ritchie. 1968. Manual of the vascular flora of the Carolinas. Chapel Hill, NC: The University of North Carolina Press. 1183 p. [7606]
109. Ramsey, Gwynn W.; Leys, Charles H.; Wright, Robert A. S.; Coleman, Douglas A.; Neas, Aubrey O.; Stevens, Charles E. 1993. Vascular flora of the James River Gorge watersheds in the central Blue Ridge Mountains of Virginia. Castanea. 58(4): 260-300. [71706]
110. Raunkiaer, C. 1934. The life forms of plants and statistical plant geography. Oxford: Clarendon Press. 632 p. [2843]
111. Reilly, Matthew J.; Wimberly, Michael C.; Newell, Claire L. 2006. Wildfire effects on plant species richness at multiple spatial scales in forest communities of the southern Appalachians. Journal of Ecology. 94(1): 118-130. [60033]
112. Remaley, Tom. 2005. Fact sheet: Princess tree--Paulownia tomentosa (Thunb.) Sieb. & Zucc. ex Steud., [Online]. In: Weeds gone wild: Alien plant invaders of natural areas. The Plant Conservation Alliance's Alien Plant Working Group (Producer). Available: [2009, March 23]. [72026]
113. Robinson, George R.; Handel, Steven N. 1993. Forest restoration on a closed landfill: rapid addition of new species by bird dispersal. Conservation Biology. 7(2): 271-278. [22062]
114. San Miguel Anyanz, A. 1985. Germination, sowing, production of seedlings, staking, and growth of Paulownia tomentosa. Comunicaciones INIA Recursos Naturales. 37: 213-219. [72087]
115. Sand, Susan. 1992. The empress tree. American Horticulturist. 71: 27-29. [72604]
116. Sanderson, Kenneth C. 1972. Effect of photoperiod on the growth of empress tree, Paulownia tomentosa, seedlings. In: Research results for nurserymen. Horticultural Series No. 18. Auburn, AL: Auburn Univeristy, Agricultural Experiment Station: 10-11. [72962]
117. Shelter, Stanwyn G.; Orli, Sylvia S.; Wells, Elizabeth F.; Beyersdorfer, Marcie. 2006. Checklist of the vascular plants of Plummers Island, Maryland. Bulletin of the Biological Society of Washington. 14(1): 1-57. [72486]
118. Simberloff, Daniel. 2000. Global climate change and introduced species in United States forests. The Science of the Total Environment. 262: 253-261. [51502]
119. Smith, Jane Kapler; Zouhar, Kristin; Sutherland, Steve; Brooks, Matthew L. 2008. Fire and nonnative invasive plants--introduction. In: Zouhar, Kristin; Smith, Jane Kapler; Sutherland, Steve; Brooks, Matthew L., eds. Wildland fire in ecosystems: fire and nonnative invasive plants. Gen. Tech. Rem. RMRS-GTR-42-vol. 6. Ogden, UT: U.S. Department of Agriculture, Forest Service, Rocky Mountain Research Station: 1-6. [70898]
120. South Carolina Exotic Pest Plant Council. 2008. Invasive plant list, [Online]. South Carolina Exotic Pest Plant Council (Producer). Available: [2009, January 5]. [72717]
121. Southeast Exotic Pest Plant Council, Tennessee Chapter. 2001. Invasive exotic pest plants in Tennessee, [Online]. Athens, GA: University of Georgia; Southeast Exotic Pest Plant Council (Producer). Available: [2004, February 12]. [46747]
122. Stalter, Robert. 1982. Some ecological observations of Delaware forests. Castanea. 47(1): 105-114. [72120]
123. Stearns, Joseph L. 1944. Paulownia as a tree of commerce. American Forests. 52(2): 60-61, 95-96. [72729]
124. Steury, Brent W.; Fleming, Gary P.; Strong, Mark T. 2008. An emendation of the vascular flora of Great Falls Park, Fairfax County, Virginia. Castanea. 73(2): 123-149. [72479]
125. Stickney, Peter F. 1989. Seral origin of species comprising secondary plant succession in Northern Rocky Mountain forests. FEIS workshop: Postfire regeneration. Unpublished draft on file at: U.S. Department of Agriculture, Forest Service, Intermountain Research Station, Fire Sciences Laboratory, Missoula, MT. 10 p. [20090]
126. Strausbaugh, P. D.; Core, Earl L. 1977. Flora of West Virginia. 2nd ed. Morgantown, WV: Seneca Books, Inc. 1079 p. [23213]
127. Stringer, Jeffrey W. 1986. A practical method for production of Paulownia tomentosa. Tree Planters' Notes. 37(2): 8-11. [72088]
128. Suiter, Dale W.; Evans, Dan K. 1999. Vascular flora and rare species of New River Gorge National River, West Virginia. Castanea. 64(1): 23-49. [71705]
129. Tackett, Edward M.; Graves, Donald H. 1983. Evaluation of direct-seeding of tree species on surface mine spoils after five years. In: Symposium on surface mining, hydrology, sedimentology and reclamation: Proceedings; 1983 November 27 - December 2; Lexington, KY. [Lexington, KY]: [University of Kentucky, College of Engineering]: 437-441. [72089]
130. Tang, R. C.; Carpenter, S. B.; Wittwer, R. F.; Graves, D. H. 1980. Paulownia -- a crop tree for wood products and reclamation of surface-mined land. Southern Journal of Applied Forestry. 4: 19-24. [72627]
131. Taverna, Kristin; Peet, Robert K.; Phillips, Laura C. 2005. Long-term change in ground-layer vegetation of deciduous forests of the North Carolina Piedmont, USA. Journal of Ecology. 93: 202-213. [51495]
132. Todorovic, Sladana; Giba, Zlatko; Zivkovic, Suzana; Grubisic, Dragoljub. 2005. Stimulation of empress tree seed germination by liquid smoke. Plant Growth Regulation. 47(2-3): 141-148. [72092]
133. Torbert, John L.; Johnson, James E. 1990. Guidelines for establishing Paulownia tomentosa on reclaimed mine soils. Information for the Virginia Coalfields--Powell River Project Series: Publication 460-118. Blacksburg, VA: Virginia Polytechnic Institute and State University; Virginia Cooperative Extension Service. 4 p. [72093]
134. Tu, Mandy. 2002. Weed notes: Paulownia tomentosa (princess tree, empress tree, royal paulownia), [Online]. In: Invasive plant management--Control methods: Plants. Davis, CA: The Nature Conservancy, Global Invasive Species Team (Producer). Available: [2009, March 3]. [72029]
135. Tu, Mandy; Hurd, Callie; Randall, John M., eds. 2001. Weed control methods handbook: tools and techniques for use in natural areas. Davis, CA: The Nature Conservancy. 194 p. [37787]
136. Turner, Gregory D.; Lau, Robyne R.; Young, Donald R. 1988. Effect of acidity on germination and seedling growth of Paulownia tomentosa. Journal of Applied Ecology. 25(2): 561-567. [72094]
137. U.S. Department of Agriculture, Forest Service, Eastern Region. 2004. Eastern Region invasive plants ranked by degree of invasiveness, [Online]. In: Noxious weeds and non-native invasive plants. Section 3: Invasive plants. Milwaukee, WI: Eastern Region (Producer). Available: /r9/wildlife/range/weed/Sec3B.htm [2004, February 16]. [46748]
138. U.S. Department of Agriculture, Forest Service, Northeastern Area. 1981. Royal paulownia: Paulownia tomentosa. Trees for reclamation: No. 18. Broomhall, PA: U.S. Department of Agriculture, Forest Service, Northeastern Area Station. 2 p. [72294]
139. U.S. Department of Agriculture, Forest Service. 2001. Guide to noxious weed prevention practices. Washington, DC: U.S. Department of Agriculture, Forest Service. 25 p. Available online: /rangelands/ftp/invasives/documents/GuidetoNoxWeedPrevPractices_07052001.pdf [2005, October 25]. [37889]
140. U.S. Department of Agriculture, Natural Resources Conservation Service. 2009. PLANTS Database, [Online]. Available: /. [34262]
141. Van Driesche, Roy; Lyon, Suzanne; Blossey, Bernd; Hoddle, Mark; Reardon, Richard, tech. coords. 2002. Biological control of invasive plants in the eastern United States. USDA Forest Service Publication FHTET-2002-04. [Washington, DC]: U.S. Department of Agriculture, Forest Service. 413 p. Available online: [2005, August 12]. [54194]
142. Virginia Department of Conservation and Recreation, Division of Natural Heritage. 2003. Invasive alien plant species of Virginia, [Online]. Virginia Native Plant Society (Producer). Available: [2009, March 23]. [44942]
143. Vogel, Willis G. 1981. A guide for revegetating coal mine soils in the eastern United States. Gen. Tech. Rep. NE-68. Broomall, PA: U.S. Department of Agriculture, Forest Service, Northeastern Forest Experiment Station. 190 p. [15576]
144. Webster, Christopher R.; Jenkins, Michael A.; Jose, Shibu. 2006. Woody invaders and the challenges they pose to forest ecosystems in the eastern United States. Journal of Forestry. 104(7): 366-374. [65270]
145. White, T. A.; Rolfe, G. L.; Bluhm, D. R. 1982. The effects of some preemergent herbicides on survival and tolerance of various woody biomass species: 1979 herbicide trials. Forestry Research Report No. 82-5. Urbana-Champaign, IL: University of Illinois; Illinois Agricultural Experiment Station. 4 p. [72735]
146. Williams, Charles E. 1993. Age structure and importance of naturalized Paulownia tomentosa in a central Virginia streamside forest. Castanea. 58(4): 243-249. [72096]
147. Williams, Charles E. 1993. The exotic empress tree, Paulownia tomentosa: an invasive pest of forests? Natural Areas Journal. 13(3): 221-222. [22468]
148. Williams, Charles E. 1998. History and status of Table Mountain pine - pitch pine forests of the southern Appalachian Mountains (USA). Natural Areas Journal. 18(1): 81-90. [27900]
149. Wilson, Geoff. 1985. China's tree-growing revolution. Australian Forest Grower. September: 16-18, 22. [72776]
150. Wilson, Larry M. 1976. A distributional survey of the vascular plants of Sandy Branch in the Loess Bluff Area of Carlisle County, Kentucky. Murray, KY: Murray State University. 163 p. Thesis. [72791]
151. Wilson, Linda M.; McCaffrey, Joseph P. 1999. Biological control of noxious rangeland weeds. In: Sheley, Roger L.; Petroff, Janet K., eds. Biology and management of noxious rangeland weeds. Corvallis, OR: Oregon State University Press: 97-115. [35715]
152. Woods, Frank W. 1989. Control of Paulownia tomentosa and Microstegium vimineum in national parks. [Report to the Great Smoky Mountains National Park]. Knoxville, TN: The University of Tennessee, Department of Forestry, Wildlife and Fisheries. 24 p. [72031]
153. Wunderlin, Richard P.; Hansen, Bruce F. 2003. Guide to the vascular plants of Florida. 2nd edition. Gainesville, FL: The University of Florida Press. 787 p. [69433]
154. Yin, R.; He, Q. 1997. The spatial and temporal effects of paulownia intercropping: The case of northern China. Agroforestry Systems. 37: 91-109. [72769]
155. Young, James A.; Young, Cheryl G. 1992. Seeds of woody plants in North America: Revised and enlarged edition. Portland, OR: Dioscorides Press. 407 p. [72640]
156. Youtie, Berta; Soll, Jonathan. 1990. Diffuse knapweed control on the Tom McCall Preserve and Mayer State Park. Unpublished report prepared for the Mazama Research Committee. On file at: U.S. Department of Agriculture, Forest Service, Rocky Mountain Research Station, Fire Sciences Laboratory, Missoula, MT. 18 p. [38353]
157. Zhen, Liu. 1999. Effect of prechilling on the germination of seeds of Paulownia tomentosa. Acta Agriculturae. 33(3): 279-281. [72072]
158. Zhu, Zhao-Hua; Chao, Ching-Ju; Lu, Xin-Yu; Xiong, Yao Gao. 1986. Paulownia in China: cultivation and utilization. Chinese Academy of Forestry Report. Beijing: Asian Network for Biological Sciences; International Development Research Centre. 65 p. [72702]

FEIS Home Page