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Ecological site R107XA211IA

Footslope Prairie

Last updated: 5/21/2020
Accessed: 11/13/2024

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General information

Provisional. A provisional ecological site description has undergone quality control and quality assurance review. It contains a working state and transition model and enough information to identify the ecological site.

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Figure 1. Mapped extent

Areas shown in blue indicate the maximum mapped extent of this ecological site. Other ecological sites likely occur within the highlighted areas. It is also possible for this ecological site to occur outside of highlighted areas if detailed soil survey has not been completed or recently updated.

MLRA notes

Major Land Resource Area (MLRA): 107X–Iowa and Missouri Deep Loess Hills

The Iowa and Minnesota Loess Hills (MLRA 107A) includes the Northwest Iowa Plains, Inner Coteau, and Coteau Moraines landforms (Prior 1991; MDNR 2005). It spans two states (Iowa, 89 percent; Minnesota, 11 percent), encompassing approximately 4,470 square miles (Figure 1). The elevation ranges from approximately 1,700 feet above sea level (ASL) on the highest ridges to about 1,115 feet ASL in the lowest valleys. Local relief is mainly 10 to 100 feet. However, some valley floors can range from 80 to 200 feet, while some upland flats only range between 3 and 6 feet. The eastern half of the MLRA is underlain by Wisconsin-age till, deposited between 20,000 and 30,000 years ago and is known as the Sheldon Creek Formation. The western half is underlain by Pre-Illinoian glacial till, deposited more than 500,000 years ago and has since undergone extensive erosion and dissection. Both surfaces are covered by approximately 4 to 20 feet of loess on the hillslopes, and Holocene alluvium covers the till in the drainageways. Cretaceous bedrock, comprised of sandstone and shale, lies beneath the glacial material (USDA-NRCS 2006).

The vegetation in the MLRA has undergone drastic changes over time. Spruce forests dominated the landscape 30,000 to 21,500 years ago. As the last glacial maximum peaked 21,500 to 16,000 years ago, they were replaced with open tundras and parklands. The end of the Pleistocene Epoch saw a warming climate that initially prompted the return of spruce forests, but as the warming continued, spruce trees were replaced by deciduous trees (Baker et al. 1990). Not until approximately 9,000 years ago did the vegetation transition to prairies as climatic conditions continued to warm and subsequently dry. Between 4,000 and 3,000 years ago, oak savannas began intermingling within the prairie landscape, while the more wooded and forested areas maintained a foothold in sheltered areas. This prairie-forest transition ecosystem formed the dominant landscapes until the arrival of European settlers (Baker et al. 1992).

Classification relationships

U.S. Forest Service Ecological Subregions: North Central Glaciated Plains (251B) Section, Outer Coteau des Prairies (251Bb), Northwest Iowa Plains (251Bd) Subsections (Cleland et al. 2007)

U.S. EPA Level IV Ecoregion: Loess Prairies (47a) (USEPA 2013)

National Vegetation Classification – Ecological Systems: Northern Tallgrass Prairie (CES205.686) (NatureServe 2015)

National Vegetation Classification – Plant Associations: Andropogon gerardii – Hesperostipa spartea – Sporobolus heterolepis Grassland (CEGL002499) (NatureServe 2015)

Biophysical Settings: Northern Tallgrass Prairie (BpS 4214200) (LANDFIRE 2009)

Natural Resources Conservation Service – Iowa Plant Community Species List: Prairie, Northern Mesic Tallgrass (USDA-NRCS 2007)

Iowa Department of Natural Resources: Blacksoil Tallgrass Prairie (INAI 1984)

Minnesota Department of Natural Resources: Ups23a Mesic Prairie (Southern) (MDNR 2005)

Ecological site concept

Footslope Prairies are located within the green areas on the map (Figure 1). They occur on alluvial fans and the soils are Mollisols that are moderately well to well-drained and deep, formed in colluvium. These fine-silty to fine-loamy soils have organic-rich surfaces with high base saturation and will intermittently dry out for periods during the summer season (MDNR 2005; NatureServe 2015).

The historic pre-European settlement vegetation on this site was dominated by herbaceous species typical of a mesic tallgrass prairie. Big bluestem (Andropogon gerardii Vitman) and little bluestem (Schizachyrium scoparium (Michx.) Torr.) are the dominant grasses of Footslope Prairies. Other grasses that may occur include porcupinegrass (Hesperostipa spartea (Trin.) Barkworth), Leiberg’s panicum (Dichanthelium leibergii (Vasey) Freckmann), and Heller’s rosette grass (Dichanthelium oligosanthes (Schult.) Gould) (MDNR 2005). Forbs typical of an undisturbed plant community associated with this ecological site include dotted blazing star (Liatris punctata Hook.), prairie violet (Viola pedatifida G. Don), Leonard’s skullcap (Scutellaria parvula Michx. Var. missouriensis (Torr.) Goodman & C.A. Lawson), and compassplant (Silphium laciniatum L.) (Drobney et al. 2001). Fire is the primary disturbance factor that maintains this site, while drought and herbivory are secondary factors (MDNR 2005; LANDFIRE 2009).

Associated sites

R107XA203IA	Calcareous Till Exposed Backslope Prairie Glacial till on upland backslopes that are shallow to calcium carbonates including Cornell, Moneta, Steinauer, and Soils that are moderately deep to carbonates
R107XA212IA	Stream Terrace Prairie Loamy alluvium over outwash including Allendorf, Estherville, Fairhaven, Hawick, Salida, and Wadena

R107XA203IA

Calcareous Till Exposed Backslope Prairie

Glacial till on upland backslopes that are shallow to calcium carbonates including Cornell, Moneta, Steinauer, and Soils that are moderately deep to carbonates

R107XA212IA

Stream Terrace Prairie

Loamy alluvium over outwash including Allendorf, Estherville, Fairhaven, Hawick, Salida, and Wadena

Similar sites

R107XA203IA	Calcareous Till Exposed Backslope Prairie Calcareous Till Exposed Backslope Prairies occur directly upland and are the colluvial source of Footslope Prairies

R107XA203IA

Calcareous Till Exposed Backslope Prairie

Calcareous Till Exposed Backslope Prairies occur directly upland and are the colluvial source of Footslope Prairies

Table 1. Dominant plant species

Tree	Not specified
Shrub	Not specified
Herbaceous	(1) Andropogon gerardii (2) Schizachyrium scoparium

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Physiographic features

Footslope Prairies occur on alluvial fans in river valleys (Figure 2). They are situated on elevations ranging from approximately 699 to 1801 feet ASL. The site does not experience flooding but rather generates runoff to adjacent, downslope ecological sites.

Figure 2. Figure 1. Location of Footslope Prairie ecological site within MLRA 107A.

Figure 3. Figure 2. Representative block diagram of Footslope Prairie and associated ecological sites.

Table 2. Representative physiographic features

Slope shape across	(1) Concave (2) Linear
Slope shape up-down	(1) Concave (2) Linear
Landforms	(1) River valley > Alluvial fan
Runoff class	Low to medium
Elevation	699 – 1,801 ft
Slope	2 – 9%
Water table depth	48 – 80 in
Aspect	Aspect is not a significant factor

Climatic features

The Iowa and Minnesota Loess Hills falls into the hot humid continental climate (Dfa) Köppen-Geiger climate classification (Peel et al. 2007). In winter, dry, cold air masses periodically shift south from Canada. As these air masses collide with humid air, snowfall and rainfall result. In summer, moist, warm air masses from the Gulf of Mexico migrate north, producing significant frontal or convective rains. Occasionally, hot, dry winds originating from the Desert Southwest will stagnate over the region, creating extended droughty periods in the summer from unusually high temperatures. Air masses from the Pacific Ocean can also spread into the region and dominate producing mild, dry weather in the autumn known as Indian Summers (NCDC 2006).

The soil temperature regime of MLRA 107A is classified as mesic, where the mean annual soil temperature is between 46 and 59°F (USDA-NRCS 2006). Temperature and precipitation occur along a north-south gradient, where temperature and precipitation increase the further south one travels. The average freeze-free period of this ecological site is about 157 days, while the frost-free period is about 134 days (Table 2). The majority of the precipitation occurs as rainfall in the form of convective thunderstorms during the growing season. Average annual precipitation is approximately 32 inches, which includes rainfall plus the water equivalent from snowfall. The average annual low and high temperatures are 36 and 58°F, respectively (Table 3).

Climate data and analyses are derived from 30-year averages gathered from two National Oceanic and Atmospheric Administration (NOAA) weather stations contained within the range of this ecological site (Table 4).

Table 3. Representative climatic features

Frost-free period (characteristic range)	126 days
Freeze-free period (characteristic range)	147-149 days
Precipitation total (characteristic range)	31 in
Frost-free period (actual range)	126 days
Freeze-free period (actual range)	147-149 days
Precipitation total (actual range)	31-32 in
Frost-free period (average)	126 days
Freeze-free period (average)	148 days
Precipitation total (average)	31 in

Characteristic range

Actual range

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Figure 4. Monthly precipitation range

Characteristic range

Actual range

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Figure 5. Monthly minimum temperature range

Characteristic range

Actual range

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Figure 6. Monthly maximum temperature range

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Figure 7. Monthly average minimum and maximum temperature

Figure 8. Annual precipitation pattern

Figure 9. Annual average temperature pattern

Climate stations used

(1) CHEROKEE [USC00131442], Cherokee, IA
(2) SIOUX RAPIDS 4 E [USC00137726], Sioux Rapids, IA

Influencing water features

Footslope Prairies are not influenced by wetland or riparian water features. Precipitation is the main source of water for this ecological site. Infiltration is moderate (Hydrologic Groups B) for undrained soils, and surface runoff is low to medium. Precipitation infiltrates the soil surface and percolates downward through the horizons unimpeded by any restrictive layer. The Dakota bedrock aquifer underlying this ecological site is typically deep and confined, leaving it generally unaffected by recharge (Prior et al. 2003). Surface runoff contributes some water to downslope ecological sites (Figure 5).

Figure 10. FIgure 5. Hydrologic cycling in Footslope Prairie ecological site.

Soil features

Soils of Footslope Prairies are in the Mollisols orders, further classified as Cumulic Hapludolls with moderate infiltration and low to medium runoff potential. The soil series associated with this site includes Ely, Judson, and Terril (Figure 6). The parent material is colluvium and the soils are moderately well to well-drained and deep. Soil pH classes are slightly acid to moderately alkaline. No rooting restrictions are noted for the soils of this ecological site (Table 5).

Figure 11. Figure 6. Profile sketches of soil series associated with Footslope Prairie.

Table 4. Representative soil features

Parent material	(1) Colluvium
Family particle size	(1) Fine-silty (2) Fine-loamy
Drainage class	Moderately well drained to well drained
Permeability class	Slow to moderately slow
Soil depth	80 in
Surface fragment cover >3"	2 – 3%

Ecological dynamics

The information in this Ecological Site Description, including the state-and-transition model (STM), was developed based on historical data, current field data, professional experience, and a review of the scientific literature. As a result, all possible scenarios or plant species may not be included. Key indicator plant species, disturbances, and ecological processes are described to inform land management decisions.

MLRA 107A is defined by a relatively low relief landscape that experiences lower rainfall amounts and available moisture compared to other MLRAs occurring to the south and east. As a result, prairie vegetation communities dominate the uplands, while forested communities are restricted to medium and large streams (Prior 1991; Eilers and Roosa 1994; MDNR 2017a, b). Footslope Prairies form an aspect of this vegetative continuum. This ecological site occurs on alluvial fans on moderately well to well-drained soils. Species characteristic of this ecological site consist of mesic, tallgrass herbaceous vegetation.

Fire is the dominant ecosystem driver for maintaining the vegetation of Footslope Prairies. Fire intensity typically consisted of periodic, high severity surface fires occurring every 1 to 5 years (LANDFIRE 2009). Ignition sources included summertime lightning strikes from convective storms and bimodal, human ignitions during the spring and fall seasons. Native Americans regularly set fires to improve sight lines for hunting, driving large game, improving grazing and browsing habitat, agricultural clearing, and enhancing vital ethnobotanical plants (Barrett 1980).

Drought and herbivory have also played a role in shaping this ecological site. The periodic episodes of reduced soil moisture in conjunction with the moderately well to well-drained soils have favored the proliferation of plant species tolerant of such conditions. Drought can also slow the growth of plants and result in dieback of certain species. The steep slopes of this ecological site likely deterred extensive grazing, however some grazing could be expected from bison (Bos bison) and possibly prairie elk (Cervus elaphus), the main herbivores in northern tallgrass prairies (LANDFIRE 2009). When coupled with fire, periods of drought and herbivory can greatly delay the establishment of woody vegetation (Pyne et al. 1996).

Today, Footslope Prairies are limited in their extent, having been reduced as a result of eastern redcedar (Juniperus virginiana L.) encroachment from long-term fire suppression or having been converted to pasture or cropland. Remnants that do exist show evidence of indirect anthropogenic influence as some non-native species are present in the species composition. A return to the historic plant community is highly challenging, but long-term reconstruction efforts can help to restore some of the natural diversity and ecological function. The state-and-transition model that follows provides a detailed description of each state, community phase, pathway, and transition. This model is based on available experimental research, field observations, literature reviews, professional consensus, and interpretations.

State and transition model

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State 1
Reference State

The reference plant community is categorized as a mesic tallgrass community, dominated by herbaceous vegetation. The two community phases within the reference state are dependent on fire. Regular fire intervals alter species composition, cover, and extent, as well as keep woody species from dominating. Drought and episodic grazing have more localized impacts in the reference phases, but do contribute to overall species composition, diversity, cover, and productivity.

Dominant plant species

American plum (Prunus americana), tree
western snowberry (Symphoricarpos occidentalis), shrub
big bluestem (Andropogon gerardii), other herbaceous
little bluestem (Schizachyrium), other herbaceous

Community 1.1
Big Bluestem-Little Bluestem

Big Bluestem – Little Bluestem – Sites in this reference community phase are dominated by grasses and forbs. Vegetative cover is continuous (75 to 100 percent) and grass heights are between 1.5 and 3 feet tall (MDNR 2005; LANDFIRE 2009). Big bluestem and little bluestem are the dominant grasses, but other species are present including porcupinegrass, Leiberg’s panicum, and Heller’s rosette grass. Characteristic forbs include pinnate prairie coneflower (Ratibida pinnata (Vent.) Barnhart), silverleaf Indian breadroot (Pediomelum argophyllum (Pursh) J. Grimes), and butterfly milkweed (Asclepias tuberosa L.).

Dominant plant species

big bluestem (Andropogon gerardii), other herbaceous
little bluestem (Schizachyrium), other herbaceous

Community 1.2
American Plum – Western Snowberry/Big Bluestem – Little Bluestem

American Plum – Western Snowberry/Big Bluestem – Little Bluestem – This reference community phase represents the vegetative community when the fire interval has been reduced, allowing shrubs to establish in the prairie. American plum (Prunus americana Marshall) and western snowberry (Symphoricarpos occidentalis Hook.) are the most common shrubs and can comprise up to 25 percent of the vegetative cover (MDNR 2005).

Dominant plant species

American plum (Prunus americana), tree
western snowberry (Symphoricarpos occidentalis), shrub
big bluestem (Andropogon gerardii), other herbaceous
little bluestem (Schizachyrium), other herbaceous

Pathway 1.1A
Community 1.1 to 1.2

Reduced fire return interval

Pathway 1.2A
Community 1.2 to 1.1

Increased fire return interval

State 2
Fire-Suppressed State

Fire suppression can transition the reference plant community into a semi-natural woodland state dominated by eastern redcedar (Briggs et al. 2002; Anderson 2003). Eastern redcedar is a species native to the eastern half of North America with a range spanning from Ontario east to Nova Scotia, south across the Great Plains into eastern Texas, and east to the Atlantic coast (Lawson 1990; Lee 1996). It is a long-lived (450+ years), slow-growing, fire-intolerant dioecious conifer historically found in areas that were protected from fire (e.g., bluffs, rocky hillsides, sandstone cliffs, granite outcrops, etc.) (Ferguson et al. 1968; Anderson 2003). Today, however, decades of fire suppression have allowed this species to spread, and it can now be found occupying sites with highly variable aspects, topography, soils, and formerly stable plant communities (Anderson 2003).

Dominant plant species

eastern redcedar (Juniperus virginiana), tree
big bluestem (Andropogon gerardii), other herbaceous
smooth brome (Bromus inermis), other herbaceous

Community 2.1
Eastern Redcedar/Big Bluestem-Smooth Brome

Eastern Redcedar/Big Bluestem – Smooth Brome – This community phase represents the early stages of eastern redcedar invasion into the prairie. Eastern redcedar seeds are readily eaten and transplanted by birds, allowing for rapid dispersal (MDNR 2005). Native grasses, such as big bluestem can persist, but non-native grasses, such as smooth brome (Bromus inermis L.), begin to co-dominate (MDNR 2005). Other non-native species that may occur include sweetclover (Meliltous officinalis (L.) Lam.) and crownvetch (Securigera varia (L.) Lassen).

Dominant plant species

eastern redcedar (Juniperus virginiana), tree
big bluestem (Andropogon gerardii), other herbaceous
smooth brome (Bromus inermis), other herbaceous

Community 2.2
Eastern Redcedar/Smooth Brome – Kentucky Bluegrass

Eastern Redcedar/Smooth Brome – Kentucky Bluegrass – Sites falling into this community phase have an established eastern redcedar tree canopy following numerous years of fire suppression. As the canopy increases, light availability is greatly reduced to the ground layer and soil moisture increases, allowing more shade tolerant species, such as Kentucky bluegrass (Poa pratensis L.), to replace the heliophytic prairie grasses (Gehring and Bragg 1992; MDNR 2005; Brantley and Young 2010; Pierce and Reich 2010). The continued absence of fire will allow this community to expand its range.

Dominant plant species

eastern redcedar (Juniperus virginiana), tree
smooth brome (Bromus inermis), grass
Kentucky bluegrass (Poa pratensis), grass

Pathway 2.1A
Community 2.1 to 2.2

Fire suppression in excess of 20 years

State 3
Forage State

The forage state occurs when the site is converted to a farming system that emphasizes domestic livestock production, known as grassland agriculture. Fire suppression, periodic cultural treatments (e.g., clipping, drainage, soil amendment applications, planting new species and/or cultivars, mechanical harvesting) and grazing by domesticated livestock transition and maintain this state (USDA-NRCS 2003). Early settlers seeded non-native species, such as smooth brome and Kentucky bluegrass, to help extend the grazing season (Smith 1998). Over time, as lands were continuously harvested or grazed by herds of cattle, these species were able to spread and expand across the prairie ecosystem, reducing the native species diversity and ecological function.

Community 3.1
Hayfield

Hayfield – Sites in this community phase consist of forage plants that are planted and mechanically harvested. Mechanical harvesting removes much of the aboveground biomass and nutrients that feed the soil ecosystem (Franzluebbers et al. 2000; USDA-NRCS 2003). As a result, soil biology is reduced leading to decreases in nutrient uptake by plants, soil organic matter, and soil aggregation. Frequent biomass removal can in turn reduce the site’s carbon sequestration capacity (Skinner 2008).

Community 3.2
Continuous Pastured Grazing System

Continuous Pastured Grazing System – This community phase is characterized by continuous grazing where domestic livestock graze a pasture for the entire season. Depending on stocking density, this can result in lower forage quality and productivity, weed invasions, and uneven pasture use. Continuous grazing can also increase the amount of bare ground and erosion and reduce soil organic matter, cation exchange capacity, water-holding capacity, and nutrient availability and retention (Bharati et al. 2002; Leake et al. 2004; Teague et al. 2011). Smooth brome, Kentucky bluegrass, and white clover (Trifolium repens L.) are common pasture species used in this phase. Their tolerance to continuous grazing has allowed these species to dominate, sometimes completely excluding the native vegetation.

Community 3.3
Rest-Rotation Pastured Grazing System

Rest-Rotation Pastured Grazing System – This community phase is characterized by rotational grazing where the pasture has been subdivided into several smaller paddocks. Through the development of a grazing plan, livestock utilize one or a few paddocks, while the remaining area is rested allowing plants to restore vigor and energy reserves, deepen root systems, develop seeds, as well as allow seedling establishment (Undersander et al. 2002; USDA-NRCS 2003). Rest-rotation pastured grazing systems include deferred rotation, rest rotation, high intensity – low frequency, and short duration methods. Vegetation is generally more diverse and can include orchargrass (Dactylis glomerata L.), timothy (Phleum pretense L.), red clover (Trifolium pratense L.), and alfalfa (Medicago sativa L.). The addition of native prairie species can further bolster plant diversity and, in turn, soil function. This community phase promotes numerous ecosystem benefits including increasing biodiversity, preventing soil erosion, maintaining and enhancing soil quality, sequestering atmospheric carbon, and improving water yield and quality (USDA-NRCS 2003).

Pathway 3.1A
Community 3.1 to 3.2

Mechanical harvesting is replaced with domestic livestock and continuous grazing

Pathway 3.1B
Community 3.1 to 3.3

Mechanical harvesting is replaced with domestic livestock and rest-rotational grazing

Pathway 3.2A
Community 3.2 to 3.1

Domestic livestock grazing is replaced with mechanical harvesting

Pathway 3.2B
Community 3.2 to 3.3

Implementation of rest-rotational grazing

Pathway 3.3B
Community 3.3 to 3.1

Domestic livestock grazing is replaced by mechanical harvesting

Pathway 3.3A
Community 3.3 to 3.2

Implementation of continuous grazing

State 4
Cropland State

The low topographic relief across the MLRA has resulted in nearly the entire area being converted to agriculture (Eilers and Roosa 1994). The continuous use of tillage, row-crop planting, and chemicals (i.e., herbicides, fertilizers, etc.) has effectively eliminated the reference community and many of its natural ecological functions in favor of crop production. Corn and soybeans are the dominant crops for the site, and oats (Avena L.) and alfalfa (Medicago sativa L.) may be rotated periodically. These areas are likely to remain in crop production for the foreseeable future.

Community 4.1
Conventional Tillage Field

Conventional Tillage Field – Sites in this community phase typically consist of monoculture row-cropping maintained by conventional tillage practices. They are cropped in either continuous corn or corn-soybean rotations. The frequent use of deep tillage, low crop diversity, and bare soil conditions during the non-growing season negatively impacts soil health. Under these practices, soil aggregation is reduced or destroyed, soil organic matter is reduced, erosion and runoff are increased, and infiltration is decreased, which can ultimately lead to undesirable changes in the hydrology of the watershed (Tomer et al. 2005).

Community 4.2
Conservation Tillage Field

Conservation Tillage Field – This community phase is characterized by rotational crop production that utilizes various conservation tillage methods to promote soil health and reduce erosion. Conservation tillage methods include strip-till, ridge-till, vertical-till, or no-till planting systems. Strip-till keeps seedbed preparation to narrow bands less than one-third the width of the row where crop residue and soil consolidation are left undisturbed in-between seedbed areas. Strip-till planting may be completed in the fall and nutrient application either occurs simultaneously or at the time of planting. Ridge-till uses specialized equipment to create ridges in the seedbed and vegetative residue is left on the surface in between the ridges. Weeds are controlled with herbicides and/or cultivation, seedbed ridges are rebuilt during cultivation, and soils are left undisturbed from harvest to planting. Vertical-till systems employ machinery that lightly tills the soil and cuts up crop residue, mixing some of the residue into the top few inches of the soil while leaving a large portion on the surface. No-till management is the most conservative, disturbing soils only at the time of planting and fertilizer application. Compared to conventional tillage systems, conservation tillage methods can improve soil ecosystem function by reducing soil erosion, increasing organic matter and water availability, improving water quality, and reducing soil compaction.

Community 4.3
Conservation Tillage with Cover Crop Field

Conservation Tillage with Cover Crop Field – This community phase applies conservation tillage methods as described above as well as adds cover crop practices. Cover crops typically include nitrogen-fixing species (e.g., legumes), small grains (e.g., rye, wheat, oats), or forage covers (e.g., turnips, radishes, rapeseed). The addition of cover crops not only adds plant diversity but also promotes soil health by reducing soil erosion, limiting nitrogen leaching, suppressing weeds, increasing soil organic matter, and improving the overall soil ecosystem. In the case of small grain cover crops, surface cover and water infiltration are increased, while forage covers can be used to graze livestock or support local wildlife. Of the three community phases for this state, this phase promotes the greatest soil sustainability and improves ecological functioning within a cropland system.

Pathway 4.1A
Community 4.1 to 4.2

Less tillage, residue management

Pathway 4.1B
Community 4.1 to 4.3

Less tillage, residue management and implementation of cover cropping

Pathway 4.2A
Community 4.2 to 4.1

Intensive tillage, remove residue and reinitialize monoculture row cropping

Pathway 4.2B
Community 4.2 to 4.3

Implementation of row cropping

Pathway 4.3B
Community 4.3 to 4.1

Intensive tillage, remove residue and reinitialize monoculture row cropping

Pathway 4.3A
Community 4.3 to 4.2

Remove cover cropping

State 5
Reconstructed Tallgrass Prairie State

Prairie reconstructions have become an important tool for repairing natural ecological functions and providing habitat protection for numerous grassland dependent species. Because the historic plant and soil biota communities of the tallgrass prairie were highly diverse with complex interrelationships, historic prairie replication cannot be guaranteed on landscapes that have been so extensively manipulated for extended timeframes (Kardol and Wardle 2010; Fierer et al. 2013). Therefore, ecological restoration should aim to aid the recovery of degraded, damaged, or destroyed ecosystems. A successful restoration will have the ability to structurally and functionally sustain itself, demonstrate resilience to the natural ranges of stress and disturbance, and create and maintain positive biotic and abiotic interactions (SER 2002). The reconstructed hill prairie state is the result of a long-term commitment involving a multi-step, adaptive management process. Diverse, species-rich seed mixes are important to utilize as they allow the site to undergo successional stages that exhibit changing composition and dominance over time (Smith et al. 2010). On-going management via prescribed fire and/or light grazing can help the site progress from an early successional community dominated by annuals and some weeds to a later seral stage composed of native, perennial grasses, forbs, and a few shrubs. Establishing a prescribed fire regimen that mimics natural disturbance patterns can increase native species cover and diversity while reducing cover of non-native forbs and grasses. Light grazing alone can help promote species richness, while grazing accompanied with fire can control the encroachment of woody vegetation (Brudvig et al. 2007).

Community 5.1
Early Successional Prairie

Early Successional Reconstructed Prairie – This community phase represents the early community assembly from prairie reconstruction and is highly dependent on the seed mix utilized and the timing and priority of planting operations. The seed mix should look to include a diverse mix of cool-season and warm-season annual and perennial grasses and forbs typical of the reference state (e.g., big bluestem, little bluestem, porcupinegrass, butterfly milkweed, pinnate prairie coneflower). Cool-season annuals can help provide litter that promotes cool, moist soil conditions to the benefit of the other species in the seed mix. The first season following site preparation and seeding will typically result in annuals and other volunteer species forming a majority of the vegetative cover. Control of non-native species, particularly perennial species, is crucial at this point to ensure they do not establish before the native vegetation (Martin and Wilsey 2012). After the first season, native warm-season grasses should begin to become more prominent on the landscape.

Community 5.2
Late Successional Reconstructed Prairie

Late Successional Reconstructed Prairie – Appropriately timed disturbance regimes (e.g., prescribed fire) applied to the early successional community phase can help increase the beta diversity, pushing the site into a late successional community phase over time. While prairie communities are dominated by grasses, these species can suppress forb establishment and reduce overall diversity and ecological function (Martin and Wilsey 2006; Williams et al. 2007). Reducing accumulated plant litter from perennial bunchgrasses allows more light and nutrients to become available for forb recruitment, allowing greater ecosystem complexity (Wilsey 2008).

Pathway 5.1A
Community 5.1 to 5.2

Invasive species control and implementation of disturbance regimes

Pathway 5.2A
Community 5.2 to 5.1

Drought or improper timing/use of management actions

Transition T1A
State 1 to 2

Long term fire suppression, land abandonment and/or overgrazing

Transition T1B
State 1 to 3

Cultural treatments are implemented to increase forage quality and yield

Transition T1C
State 1 to 4

Intensive tillage, initiate monoculture row cropping

Restoration pathway R2A
State 2 to 1

Woody species removal and reintroduction of fire

Transition T2A
State 2 to 3

Cultural treatments are implemented to increase forage quality and yield

Transition T2B
State 2 to 4

Cultural treatments are implemented to increase forage quality and yield

Transition R2B
State 2 to 5

Site preparation, invasive species control and native seeding

Restoration pathway T3A
State 3 to 2

Long-term fire suppression, land abandonment and/or overgrazing

Transition T3B
State 3 to 4

Intensive tillage

Transition R3A
State 3 to 5

Site preparation, invasive species control and native seeding

Restoration pathway T4A
State 4 to 2

Long-term fire suppression, land abandonment, and/or overgrazing

Restoration pathway T4B
State 4 to 3

Cultural treatments are implemented to increase forage quality and yield

Transition R4A
State 4 to 5

Site preparation, invasive species control and native seeding

Restoration pathway T5A
State 5 to 2

Long-term fire suppression, land abandonment and/or grazing

Restoration pathway T5B
State 5 to 3

Cultural treatments are implemented to increase forage quality and yield

Restoration pathway T5C
State 5 to 4

Intensive tillage, reinitialize monoculture row cropping

Additional community tables

Supporting information

Inventory data references

Tier 3 Sampling Plot used to develop the reference state, community phase 1.2:
State County Ownership Legal Description Easting Northing
Iowa O’Brien Thompson Quarry Prairie Wildlife Area – Iowa Department of Natural Resources T94N R39W S11 302485 4761338

Other references

Anderson, M.D. 2003. Juniperus virginiana. In: Fire Effects Information System [Online]. U.S. Department of Agriculture, Forest Service, Rocky Mountain Research Station, Fire Sciences Laboratory (Producer). Available at: https://www.feis-crs.org/feis/. (Accessed 12 February 2018).

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Briggs, J.M., A.K. Knapp, and B.L. Brock. 2002. Expansion of woody plants in tallgrass prairie: a fifteen-year study of fire and grazing-interactions. The American Midland Naturalist 147: 287-294.

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Drobney, P.D., G.S. Wilhelm, D. Horton, M. Leoschke, D. Lewis, J. Pearson, D. Roosa, and D. Smith. 2001. Floristic Quality Assessment for the State of Iowa. Neal Smith National Wildlife Refuge and Ada Hayden Herbarium, Iowa State University, Ames, IA. 123 pps.

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Franzluebbers, A.J., J.A. Stuedemann, H.H. Schomberg, and S.R. Wilkinson. 2000. Soil organic C and N pools under long-term pasture management in the Southern Piedmont USA. Soil Biology and Biochemistry 32:469-478.

Gehrig, J.T. and T.B. Bragg. 1992. Changes in prairie vegetation under eastern redcedar (Juniperus virginiana L.) in an eastern Nebraska bluestem prairie. The American Midland Naturalist 128: 209-271.

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Kardol, P. and D.A. Wardle. 2010. How understanding aboveground-belowground linkages can assist restoration ecology. Trends in Ecology and Evolution 25: 670-679.

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Contributors

Lisa Kluesner
Dan Pulido

Approval

Chris Tecklenburg, 5/21/2020

Acknowledgments

This project could not have been completed without the dedication and commitment from a variety of partners and staff (Table 6). Team members supported the project by serving on the technical team, assisting with the development of state and community phases of the state-and-transition model, providing peer review and technical editing, and conducting quality control and quality assurance reviews.

Table 6. List of primary contributors and reviewers.

Organization Name Title Location

Drake University:
Dr. Tom Rosburg, Professor of Ecology and Botany, Des Moines, IA

Iowa Department of Natural Resources:
John Pearson, Ecologist, Des Moines, IA

LANDFIRE (The Nature Conservancy):
Randy Swaty, Ecologist, Evanston, IL

Natural Resources Conservation Service:
Rick Bednarek, Iowa State Soil Scientist, Des Moines, IA
Patrick Chase, Area Resource Soil Scientist, Fort Dodge, IA
Stacey Clark, Regional Ecological Site Specialist, St. Paul, MN
James Cronin, State Biologist, Des Moines, IA
Tonie Endres, Senior Regional Soil Scientist, Indianapolis, IN
John Hammerly, Soil Data Quality Specialist, Indianapolis, IN
Lisa Kluesner, Ecological Site Specialist, Waverly, IA
Sean Kluesner, Earth Team Volunteer, Waverly, IA
Jeff Matthias, State Grassland Specialist, Des Moines, IA
Louis Moran, PhD, Area Resource Soil Scientist, Sioux City, IA
Kevin Norwood, Soil Survey Regional Director, Indianapolis, IN
Doug Oelmann, Soil Scientist, Des Moines, IA
James Phillips, GIS Specialist, Des Moines, IA
Dan Pulido, Soil Survey Leader, Atlantic, IA
Jason Steele, Area Resource Soil Scientist, Fairfield, IA
Doug Wallace, Ecological Site Specialist, Columbia, MO

Rangeland health reference sheet

Interpreting Indicators of Rangeland Health is a qualitative assessment protocol used to determine ecosystem condition based on benchmark characteristics described in the Reference Sheet. A suite of 17 (or more) indicators are typically considered in an assessment. The ecological site(s) representative of an assessment location must be known prior to applying the protocol and must be verified based on soils and climate. Current plant community cannot be used to identify the ecological site.

Author(s)/participant(s)
Contact for lead author
Date	09/16/2022
Approved by	Chris Tecklenburg
Approval date
Composition (Indicators 10 and 12) based on	Annual Production

Indicators

Number and extent of rills:
Presence of water flow patterns:
Number and height of erosional pedestals or terracettes:
Bare ground from Ecological Site Description or other studies (rock, litter, lichen, moss, plant canopy are not bare ground):
Number of gullies and erosion associated with gullies:
Extent of wind scoured, blowouts and/or depositional areas:
Amount of litter movement (describe size and distance expected to travel):
Soil surface (top few mm) resistance to erosion (stability values are averages - most sites will show a range of values):
Soil surface structure and SOM content (include type of structure and A-horizon color and thickness):
Effect of community phase composition (relative proportion of different functional groups) and spatial distribution on infiltration and runoff:
Presence and thickness of compaction layer (usually none; describe soil profile features which may be mistaken for compaction on this site):
Functional/Structural Groups (list in order of descending dominance by above-ground annual-production or live foliar cover using symbols: >>, >, = to indicate much greater than, greater than, and equal to):

Dominant:

Sub-dominant:

Other:

Additional:
Amount of plant mortality and decadence (include which functional groups are expected to show mortality or decadence):
Average percent litter cover (%) and depth ( in):
Expected annual annual-production (this is TOTAL above-ground annual-production, not just forage annual-production):
Potential invasive (including noxious) species (native and non-native). List species which BOTH characterize degraded states and have the potential to become a dominant or co-dominant species on the ecological site if their future establishment and growth is not actively controlled by management interventions. Species that become dominant for only one to several years (e.g., short-term response to drought or wildfire) are not invasive plants. Note that unlike other indicators, we are describing what is NOT expected in the reference state for the ecological site:
Perennial plant reproductive capability:

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Natural ResourcesConservation Service

Ecological site R107XA211IA

Footslope Prairie

Last updated: 5/21/2020 Accessed: 11/13/2024

General information

Figure 1. Mapped extent

MLRA notes

Classification relationships

Ecological site concept

Associated sites

Similar sites

Table 1. Dominant plant species

Ecosystem states

States 2 and 5 (additional transitions)

State 1 submodel, plant communities

State 2 submodel, plant communities

State 3 submodel, plant communities

State 4 submodel, plant communities

State 5 submodel, plant communities

Natural Resources
Conservation Service

Last updated: 5/21/2020
Accessed: 11/13/2024